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SOCIETY OF ECOLOGICAL CHEMISTRY AND ENGINEERING
ECOLOGICAL CHEMISTRY
AND ENGINEERING A
CHEMIA I IN¯YNIERIA EKOLOGICZNA A
Vol. 18
No. 4
OPOLE 2011
EDITORIAL COMMITTEE
Witold Wac³awek (University, Opole, PL) – Editor-in-Chief
Milan Kraitr (Western Bohemian University, Plzen, CZ)
Jerzy Skrzypski (University of Technology, £ódŸ, PL)
Maria Wac³awek (University, Opole, PL)
Tadeusz Majcherczyk (University, Opole, PL) – Secretary
PROGRAMMING BOARD
Witold Wac³awek (University, Opole, PL) – Chairman
Jerzy Bartnicki (Meteorological Institute – DNMI, Oslo-Blindern, NO)
Mykhaylo Bratychak (National University of Technology, Lviv, UA)
Bogus³aw Buszewski (Nicolaus Copernicus University, Toruñ, PL)
Eugenija Kupcinskiene (University of Agriculture, Kaunas, LT)
Bernd Markert (International Graduate School [IHI], Zittau, DE)
Nelson Marmiroli (University, Parma, IT)
Jacek Namieœnik (University of Technology, Gdansk, PL)
Lucjan Paw³owski (University of Technology, Lublin, PL)
Krzysztof J. Rudziñski (Institute of Physical Chemistry PAS, Warszawa, PL)
Manfred Sager (Agency for Health and Food Safety, Vienna, AT)
Mark R.D. Seaward (University of Bradford, UK)
Jíøi Ševèik (Charles University, Prague, CZ)
Piotr Tomasik (University of Agriculture, Krakow, PL)
Roman Zarzycki (University of Technology, Lodz, PL)
Tadeusz Majcherczyk (University, Opole, PL) – Secretary
EDITORIAL OFFICE
Opole University
ul. kard. B. Kominka 4, 45–032 OPOLE, PL
phone +48 77 455 91 49
email: [email protected]
http://tchie.uni.opole.pl
SECRETARIES
Agnieszka Do³hañczuk-Œródka, phone +48 77 401 60 46, email: [email protected]
Ma³gorzata Rajfur, phone +48 77 401 60 42, email: [email protected]
SECRETARIES’ OFFICE
phone +48 77 401 60 42
Copyright © by
Society of Ecological Chemistry and Engineering, Opole
Ecological Chemistry and Engineering A / Chemia i In¿ynieria Ekologiczna A
is partly financed by Ministry of Science and Higher Education, Warszawa
ISSN 1898–6188
CONTENTS
Editorial
. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
495
Jakub BEKIER, Jerzy DROZD and Micha³ LICZNAR – Nitrogen Transformations
in Composts Produced from Municipal Solid Wastes . . . . . . . . . . . . . .
497
Jacek CZEKA£A – Influence of Long-Term Sprinkling Irrigation and Nitrogen
Fertilisation on Soil Nitrogen Content of a Cereal Crop Rotation . . . . . . . . .
507
Franciszek CZY¯YK and Agnieszka RAJMUND – Quantity of Nitrogen Deposited
in Soil as Precipitated from Atmosphere in the Wroclaw Area during 2002–2007
. . .
515
Tadeusz FILIPEK and Pawe³ HARASIM – Nitrogen Content and Aminoacids Protein
Composition of Grain of Winter Wheat Foliar Fertilized with Urea
and Microelements Fertilizers . . . . . . . . . . . . . . . . . . . . . . .
523
Stefan GRZEGORCZYK, Kazimierz GRABOWSKI and Jacek ALBERSKI – Nitrogen
Accumulation by Selected Species of Grassland Legumes and Herbs . . . . . . . .
531
Gra¿yna HARASIMOWICZ-HERMANN and Janusz HERMANN – Nitrogen
Bioconversion and Fodder Protein Recovery from Distillery Spent Wash . . . . . . .
537
Czes³awa JASIEWICZ and Agnieszka BARAN – Comparison of the Effect of Mineral
and Organic Fertilization on the Composition of Amino Acids in Green Biomass
Maize . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
545
Andrzej KOCOWICZ and El¿bieta JAMROZ – Carbon and Nitrogen Content
of Mountain Meadow and Forest Podzols and Brown Acid Soils . . . . . . . . .
553
Urij Anatoljevich MAZHAJSKIJ, Tatjana Mihajlovna GUSEVA, Andrej Valerjevich
ILJINSKIJ, Svetlana Valerjevna ANDRIYANEC and Ekaterina Sergeevna GUSEVA
– Influence of Heavy Metals on Microorganisms Taking Part in the Circulation
of Nitrogen in Soil . . . . . . . . . . . . . . . . . . . . . . . . . .
563
Zenia MICHA£OJÆ – Influence of Varied Doses and Forms of Microelements
and Medium on Nitrate(V) and (III) Content in Lettuce . . . . . . . . . . . . .
571
Anna MIECHÓWKA, Micha³ G¥SIOREK, Agnieszka JÓZEFOWSKA and Pawe³
ZADRO¯NY – Content of Microbial Biomass Nitrogen in Differently Used Soils
of the Carpathian Foothills
. . . . . . . . . . . . . . . . . . . . . . .
577
Lidia OKTABA and Alina KUSIÑSKA – Mineral Nitrogen in Soils of Different
Land Use . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
585
Joanna ONUCH-AMBORSKA – Effect of Different Doses of Nitrogen on Soil Quality
and Yield of Plants Grown in the Land Recultivated after Sulphur Mining . . . . . .
593
Tomasz SOSULSKI and Marian KORC – Effects of Different Mineral and Organic
Fertilization on the Content of Nitrogen and Carbon in Soil Organic Matter
Fractions . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
601
Tomasz SOSULSKI and Stanis³aw MERCIK – Dynamics of Mineral Nitrogen Movement
in the Soil Profile in Long-Term Experiments . . . . . . . . . . . . . . . .
611
Tamara PERSICOVA and Natalia POSHTOVAYA – Effectiveness of Bacterial Preparations
and Plant Growth Regulators in the Separate and Mixed Crops of Oats, Spring Wheat
and Narrow-Leaved Lupine Depending on Level of Nitrogen Nutrition . . . . . . .
619
Ewa SPYCHAJ-FABISIAK, Jacek D£UGOSZ and Krzysztof PI£AT – Spatial Variability
of Total Nitrogen in the Surface Horizon at the Production Field Scale . . . . . . .
629
Alojzy WOJTAS, Ma³gorzata D¥BEK, Gra¿yna PIOTROWSKA and Tadeusz
MALINOWSKI – Nitrogen in Water from Wells . . . . . . . . . . . . . . .
637
VARIA
Invitation for ECOpole ’11 Conference
Zaproszenie na Konferencjê ECOpole ’11
. . . . . . . . . . . . . . . . . . . .
647
. . . . . . . . . . . . . . . . . . .
649
Guide for Authors on Submission of Manuscripts
. . . . . . . . . . . . . . . .
651
Zalecenia dotycz¹ce przygotowania manuskryptów
. . . . . . . . . . . . . . . .
653
SPIS TREŒCI
Od Redakcji
. . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
495
Jakub BEKIER, Jerzy DROZD i Micha³ LICZNAR – Przemiany zwi¹zków azotu
w kompostach produkowanych ze sta³ych odpadów miejskich . . . . . . . . . . .
497
Jacek CZEKA£A – Wp³yw wieloletniego deszczowania i nawo¿enia azotem
na zawartoœæ azotu w glebie p³odozmianu zbo¿owego . . . . . . . . . . . . . .
507
Franciszek CZY¯YK i Agnieszka RAJMUND – Iloœæ azotu wnoszona do gleby
z opadami atmosferycznymi w rejonie Wroc³awia w latach 2002–2007 . . . . . . .
515
Tadeusz FILIPEK i Pawe³ HARASIM – Zawartoœæ azotu i sk³ad aminokwasowy
bia³ka ziarna pszenicy ozimej dokarmianej dolistnie mocznikiem i nawozami
mikroelementowymi . . . . . . . . . . . . . . . . . . . . . . . . . .
523
Stefan GRZEGORCZYK, Kazimierz GRABOWSKI i Jacek ALBERSKI – Gromadzenie
azotu przez wybrane gatunki roœlin motylkowatych i zió³ ³¹kowych
. . . . . . . .
531
Gra¿yna HARASIMOWICZ-HERMANN i Janusz HERMANN – Biokonwersja azotu
i odzysk bia³ka paszowego z wywaru gorzelniczego . . . . . . . . . . . . . .
537
Czes³awa JASIEWICZ i Agnieszka BARAN – Porównanie wp³ywu mineralnego
i organicznego nawo¿enia na sk³ad aminokwasów w zielonej masie kukurydzy
. . . .
545
Andrzej KOCOWICZ i El¿bieta JAMROZ – Zawartoœæ wêgla i azotu w bielicowych
i brunatnych glebach górskich pod u¿ytkowaniem darniowym oraz leœnym . . . . . .
553
Urij Anatoljevich MAZHAJSKIJ, Tatjana Mihajlovna GUSEVA, Andrej Valerjevich
ILJINSKIJ, Svetlana Valerjevna ANDRIYANEC i Ekaterina Sergeevna GUSEVA
– Wp³yw metali ciê¿kich na mikroorganizmy uczestnicz¹ce w obiegu azotu
w glebie . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
563
Zenia MICHA£OJÆ – Wp³yw zró¿nicowanych dawek i form mikroelementów
oraz pod³o¿a na zawartoœæ azotanów(V) i (III) w sa³acie . . . . . . . . . . . .
571
Anna MIECHÓWKA, Micha³ G¥SIOREK, Agnieszka JÓZEFOWSKA i Pawe³
ZADRO¯NY – Zawartoœæ azotu biomasy mikrobiologicznej w ró¿nie u¿ytkowanych
glebach Pogórza Karpackiego . . . . . . . . . . . . . . . . . . . . . . .
577
Lidia OKTABA i Alina KUSIÑSKA – Mineralne formy azotu w glebach o ró¿nym
sposobie u¿ytkowania
. . . . . . . . . . . . . . . . . . . . . . . . .
585
Joanna ONUCH-AMBORSKA – Wp³yw zró¿nicowanych dawek azotu na glebê
oraz jakoœæ roœlin uprawianych na rekultywowanych terenach górniczych . . . . . . .
593
Tomasz SOSULSKI i Marian KORC – Wp³yw zró¿nicowanego nawo¿enia mineralnego
i organicznego na zawartoœæ azotu i wêgla we frakcjach materii organicznej gleby . . .
601
Tomasz SOSULSKI i Stanis³aw MERCIK – Dynamika przemieszczania siê azotu
mineralnego w profilu glebowym w warunkach wieloletnich doœwiadczeñ
nawozowych . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
611
Tamara PERSICOVA i Natalia POSHTOVAYA – Efektywnoœæ preparatów bakteryjnych
i regulatorów wzrostu roœlin w siewach czystych i mieszanych owsa, pszenicy jarej
i ³ubinu w¹skolistnego w zale¿noœci od poziomu ¿ywienia azotem . . . . . . . . .
619
Ewa SPYCHAJ-FABISIAK, Jacek D£UGOSZ i Krzysztof PI£AT – Zmiennoœæ przestrzenna
zawartoœci azotu ogó³em w poziomie powierzchniowym w skali pola produkcyjnego . .
629
Alojzy WOJTAS, Ma³gorzata D¥BEK, Gra¿yna PIOTROWSKA i Tadeusz MALINOWSKI
– Zwi¹zki azotowe w wodach studziennych . . . . . . . . . . . . . . . . .
637
VARIA
Zaproszenie na Konferencjê ECOpole ’11
. . . . . . . . . . . . . . . . . . . .
647
. . . . . . . . . . . . . . . . . . .
649
Guide for Authors on Submission of Manuscripts
. . . . . . . . . . . . . . . .
651
Zalecenia dotycz¹ce przygotowania manuskryptów
. . . . . . . . . . . . . . . .
653
Papers published in the issue have been presented during the 3rd International
Scientific Conference on Nitrogen in Natural Environment, Olsztyn, May 21–22, 2009.
Artyku³y opublikowane w tym zeszycie by³y przedstawione w czasie III Miêdzynarodowej Konferencji Naukowej pt.: Azot w œrodowisku przyrodniczym, Olsztyn,
21–22 maja 2009 r. Organizatorem konferencji by³a Katedra Chemii Œrodowiska Uniwersytetu Warmiñsko-Mazurskiego w Olsztynie kierowana przez Pana Prof. dr. hab.
Zdzis³awa Cieæko.
Prezentowane artyku³y przesz³y normaln¹ procedurê recenzyjn¹ i redakcyjn¹.
Konferencja by³a dofinansowana przez Komitet Gleboznawstwa i Chemii Rolnej
Polskiej Akademii Nauk oraz Wojewódzki Fundusz Ochrony Œrodowiska i Gospodarki
Wodnej w Olsztynie. Dziêkujemy Sponsorom za wsparcie.
ECOLOGICAL CHEMISTRY AND ENGINEERING
A
Vol. 18, No. 4
2011
Jakub BEKIER1, Jerzy DROZD1 and Micha³ LICZNAR1
NITROGEN TRANSFORMATIONS IN COMPOSTS
PRODUCED FROM MUNICIPAL SOLID WASTES
PRZEMIANY ZWI¥ZKÓW AZOTU W KOMPOSTACH
PRODUKOWANYCH ZE STA£YCH ODPADÓW MIEJSKICH
Abstract: The aim of the research was to estimate the direction and intensity of nitrogen transformations in
composts produced from municipal solid wastes (MSW), including time, composting parameters and
composting technology. Objects of studies were composts at different maturity stages, produced according to
two different technologies: MUT-DANO in Katowice and KKO-100 in Zielona Gora. In collected samples the
following determinations were performed: temperature, humidity, pH in KCl, Corg – total organic carbon, Nt –
total nitrogen, Nw – water soluble nitrogen, N-NH4+ and N-NO3– in water extracts (compost to water ratio
1:10). Obtained results show that during composting of MSW the amounts of Nt and N-NO3– increased while
those of Nw and N-NH4+ decreased. Intensity of those changes was statistically confirmed and correlated with
composting conditions. Prolonged anaerobic conditions in material from Katowice inhibited nitrification
processes, which was confirmed by higher N-NH4+/N-NO3– ratio. To take into consideration the value of this
rate, compost from Katowice did not reach maturity even after 180 days of composting.
Keywords: composting of municipal solid wastes, nitrogen transformations
Nitrogen transformations in the course of the process of composting take place as
a result of biological processes that include ammonification, nitrification and denitrification. The resultant of those processes are changes in quantity and quality of that
macrocomponent [1]. Due to the fundamental importance of nitrogen in the determination of fertiliser quality of composts, numerous studies have been performed to date on
nitrogen transformations in the various phases of compost maturity and for various
composting conditions [2–4]. Results obtained so far indicate an increase in total
nitrogen with progress of the composting processes. However, taking into account the
nature aspect of application of composts, one should consider not only the total levels of
their components, but also of forms of those components with various levels of
availability.
1
Institute of Soil Sciences and Environmental Protection, Wroclaw University of Environmental and Life
Sciences, ul. Grunwaldzka 53, 50–357 Wroc³aw, Poland, phone: 71 320 19 02, email: [email protected]
498
Jakub Bekier et al
In spite of the studies conducted for years within this field, no optimum system of
control of nitrogen transformations during composting has been developed. This is most
likely due to the extensive variability of the morphological and chemical composition of
wastes, which makes the choice of suitable technology difficult, while application of
universal solutions not always brings the expected results. Therefore, the objective of
this study was to acquire knowledge on the intensity and directions of nitrogen
transformations during composting of municipal solid wastes by means of various
techniques.
Material and methods
The experimental materials were composts produced of solid municipal wastes
according to different technologies, those of MUT-DANO in Katowice and KKO-100
in Zielona Gora. Samples for analyses were taken at intervals of 10–14 days, in
different phases of maturation of composts on the prism. A total of 11 samples were
collected from the composting plant in Katowice, and 10 samples from that in Zielona
Gora. To identify the processes of nitrogen transformation, the following determinations
were made: temperature, pH in KCl, current moisture level, Corg – organic carbon, with
the Tiurin oxidimetric method, Nt – total nitrogen and Nw – water-soluble nitrogen
(1:10) with the Kjeldahl method on the Büchi apparatus, content of mineral forms of
nitrogen (Nmin): N-NH4+ and N-NO3– in water extracts (1:10) using ion-selective
electrodes “Elmetron”.
The obtained results permitted evaluation of the material under study on the basis of
selected chemical indices of compost maturity.
Statistical analysis was performed on the basis of mean values from three replications
for each date f analysis, while all the results were used for statistical calculation by
means of the “Statistica 7” software.
Results and discussion
Temperature is one of the most important physical criteria for the estimation of
compost maturity, and at the same a measurable indicator of the intensity of processes
of biotransformation taking place in the course of composting [1, 5, 6]. Its changes in
the course of composting are related with the metabolic activity of microorganisms
whose succession varies in a dynamic manner depending on the phase of composting.
The most important phase of composting is the thermophilic phase, when the
temperature of the composted mass reaches 55 oC.
In the case of the compost produced in Katowice, the thermophilic phase (with
temperature > 55 oC) began on the 19th day of composting and ran in 5 cycles, the
longest of which lasted 10 days, and the shortest 2 days (Fig. 1). Extended duration of
the thermophilic phase and its division into several short parts is a consequence of
incorrect care of the prism, and in particular of the neglect – in the initial weeks of
composting – of application of stirring and aeration of the composted mass. Reshuffling
of the prism was made three times, between days 60 and 65 of composting.
Nitrogen Transformations in Composts...
499
Temperature [oC]
70
50
30
Katowice
Zielona Gora
Thermophilic phase
10
0
20
40
60
80
100
120
140
160
180
Composting days
Fig. 1. Changes of the temperature during composting municipal wastes
In the compost produced in Zielona Gora, the thermophilic phase started on the 23rd
day of composting and lasted for 16 days (Fig. 1). Two cycles were observed, of 10 and
6 days, respectively. Maximum temperature of 64 oC was recorded on the 28th day of
composting. It should be emphasised that in terms of aeration and stirring the compost
prism in Zielona Gora was maintained correctly, those treatments being performed
regularly at every 10–20 days.
Based on studies performed earlier [7, 8], the moisture level of composted mass is an
important factor determining the growth and functioning of microorganisms responsible
for the processes of biotransformation. It is assumed that the most optimal water content
in composts is 400–600 mg H2O kg–1. The results obtained in this study (Fig. 2) show
that the moisture level was variable in the time of composting. In both composts it was
initially within the optimum range, between 400 and 550 mg H2O kg–1, but after the
start of the thermophilic phase, both in Katowice and in Zielona Gora, there occurred
a drop in compost moisture below 400 mg H2O kg–1 (56–70 day of composting). Return
55
Katowice
Humidity [% H2O]
50
Zielona Gora
45
40
35
30
0
20
40
60
80
100
Composting days
Fig. 2. Changes of composted municipal wastes humidity
120
140
160
180
500
Jakub Bekier et al
to the optimum level in the compost from Katowice took place as a result of a rainfall,
while in Zielona Gora artificial supplementary irrigation was applied.
Many studies [1, 3, 4] point out changes in pH that take place in the course of
composting. Those result from the varied intensity of biochemical processes during
composting, determined primarily by temperature, aeration and moisture level of the
maturing compost. The results obtained in this study clearly indicate a relation of the pH
values with the changes that take place during the termophilous phase of compost
maturation (Fig. 3). In that phase an increase in pH values was observed in both
composts under study. This was probably due to intensive release of alkaline cations as
a result of processes of mineralisation, especially of large amounts of NH3 as a result of
hydrolysis of proteins. In further phase of composting, with progressing processes of
maturation, a distinct lowering of pH was observed, followed by stabilisation of the
value of that parameter.
Organic matter contained in solid municipal wastes undergoes continuous transformation in the course of their composting. In the light of earlier studies [5, 6, 9], there
8.0
Katowice
Zielona Gora
pHKCl
7.5
7.0
6.5
6.0
0
20
40
60
80
100
120
140
160
180
Composting days
Fig. 3. Changes of pHKCl value in differently matured composts from municipal wastes
210
Katowice
Zielona Gora
Corg [g kg–1 dm]
190
170
150
130
110
90
70
0
20
40
60
80
100
120
140
160
Composting days
Fig. 4. Changes of Corg contents in differently matured composts from municipal wastes
180
501
takes place a reduction of the amount of organic matter that may even reach more than
50% of the initial value. Changes in the content of total organic carbon (Corg) during
composting of solid municipal wastes in Katowice and Zielona Gora indicate that in
both cases the loss of carbon exceeded 50% (Fig. 4, Table 1).
In the case of the compost from Zielona Gora, the values obtained and the dynamics
of changes in the content of total carbon did not differ significantly from values
obtained by other authors [6, 7, 9]. Changes in the content of Corg in the compost
produced in Katowice ran a somewhat different course. Due to the neglect concerning
the correct maintenance of the prism, there was a less pronounced effect of the
termophilic phase in the intensity of carbon mineralisation. When composting of wastes
proceeds under more anaerobic conditions, the processes of organic matter transformation are notably slowed down.
Table 1
Changes of Corg and different forms of nitrogen contents during maturity of composts
from municipal wastes
Nt
Corg
Composting
days
–1
Nw
Corg
–1
[g kg ]
Nt
–1
[mg kg ]
[mg kg–1]
[g kg ]
Katowice
Nw
Zielona Gora
1
201.7
6.4
1467.0
205.9
5.7
1433.0
14
192.0
7.7
1367.0
183.9
6.2
1380.0
28
184.9
8.0
1300.0
155.5
6.3
1306.0
42
165.0
8.6
1133.0
135.8
7.9
911.0
56
157.4
8.8
1100.0
126.1
8.2
854.0
70
146.7
9.0
1199.0
116.4
8.4
884.0
90
132.8
9.8
1200.0
106.8
9.2
805.0
107
120.4
12.6
900.0
99.1
11.9
761.0
127
110.4
13.3
800.0
92.8
12.6
667.0
150
107.0
14.1
700.0
87.8
13.4
746.0
180
100.1
14.4
667.0
—
—
—
During composting, changes were observed in the content of nitrogen and its
particular forms (Table 1). The highest levels of total nitrogen Nt were observed in the
final phase of maturation, when they amounted to 14.4 g kg–1 in the compost from
Katowice and 13.4 g kg–1 in the compost from Zielona Gora. These results are in
agreement with those of numerous earlier studies which also revealed an increase in
nitrogen content during the later phases of composting.
The different conditions prevailing in the compost prisms under study determined the
different runs of the processes of organic matter transformation that were conducive to
the formation of water-soluble forms of nitrogen (Nw). In both composts a decrease was
observed in the content of water-soluble nitrogen Nw with the progress of their
maturation (Table 1). This was probably due to the incorporation of nitrogen in the
structures of organic compounds, and of humic acids in particular.
502
Jakub Bekier et al
The highest level of the form N-NH4+ (773 mg kg–1) was recorded on the 70th day of
composting in the material from Katowice, and on the 45th day (737 mg kg–1) in the
material from Zielona Gora (Fig. 5). This may be related with intensive processes of
hydrolysis of protein substances taking place in the termophilic phase [4, 6, 7, 9].
Katowice
1000
N-NH4+
N-NO3–
600
600
400
400
200
200
0
N-NH4+
N-NO3–
800
mg kg–1
mg kg–1
800
Zielona Gora
1000
0
0
20
40
60
80 100 120 140 160 180
Composting days
0
20
40
60
80 100 120 140 160 180
Composting days
Fig. 5. Changes of mineral, water soluble nitrogen forms contents during maturity of composts from
municipal wastes
The lowest levels of that form of nitrogen, 227 mg kg–1 in the compost from
Katowice and 78 mg kg–1 in that from Zielona Gora (Fig. 5), were recorded in the final
phase of composting. The lowering in the content of the ammonium form of nitrogen
was more pronounced in the compost from Zielona Gora, which could have been
determined by more favourable aeration conditions.
The different conditions of composting were also reflected in the dynamics of
formation of the nitrate form of nitrogen. In both composts there was an increasing
trend of N-NO3– – from 8 to 634 mg kg–1 in Zielona Gora and from 7 to 210 mg kg–1 in
Katowice. The notably lower level of that form of nitrogen in the compost from
Katowice indicates an effect of insufficient aeration of that material on the quality of
compost produced. Extended anaerobic periods inhibited the processes of nitrification in
the compost from Katowice, which was manifested in a decrease in the level of the form
N-NO3– with relation to N-NH4+ (Fig. 5). These results are evidence of less favourable
direction of transformation of nitrogen compounds and at the same indicate incomplete
maturity of the compost [1, 3, 7].
Based on the results obtained, an estimation of the maturity of the composts was
performed (Table 2) taking into account the following chemical indices [3]:
– ratio of organic carbon to total nitrogen – Corg/Nt,
– oxidation index of mineral forms of nitrogen – (N-NH4+/N-NO3–),
– ratio of water-soluble nitrogen to total nitrogen – (Nw/Nt) × 100,
– index of nitrogen mineralisation in water extract – (Nmin/Nw) × 100.
When estimating composts based on the above indices, attention should be paid to
the time of composting, after which a given parameter attains relative stabilisation.
503
Table 2
Changes of chemical compost maturity indices value during composting of municipal wastes
Composting
days
Corg/Nt
(Nw/Nt) × 100
(Nmin/Nw) × 100
N-NH4+/N-NO3–
34.1
38.0
53.8
44.1
65.8
78.3
82.8
77.4
64.0
69.0
65.5
70.4
31.5
34.0
18.2
3.6
4.7
1.6
1.8
1.3
1.5
1.1
31.6
34.3
51.7
84.0
87.5
70.6
72.9
71.2
90.6
95.4
55.6
25.3
29.7
26.3
3.6
2.6
1.7
0.2
0.2
0.1
Katowice
1
14
28
42
56
70
90
107
127
150
180
31.7
24.9
23.0
19.3
17.8
16.2
13.5
9.6
8.3
7.6
7.0
1
14
28
45
56
70
90
107
127
149
36.1
29.7
24.7
17.2
15.5
13.9
11.7
8.3
7.4
6.6
23.0
17.8
16.2
13.2
12.5
13.3
12.2
7.1
6.0
5.0
4.6
Zielona Gora
25.1
22.3
20.8
11.5
10.5
10.6
8.8
6.4
5.3
5.6
One of the most frequently used parameters defining the degree of maturity of
composts is the ratio of total organic carbon to total nitrogen, Corg/Nt. It is accepted that
mature composts should have a stabilised value of that index at the level of ca 10. The
study clearly demonstrated a reduction in the value of that ratio with progressing
processes of compost maturation (Table 2). This results primarily from the notable loss
of carbon in the process of mineralisation, and from the incorporation of nitrogen into
structures of humus compounds formed in the process of humification. Analysing the
run of changes in the values of that index during composting one can demonstrate that
in both composts distinct stabilisation was observed after about 90 days, with a slight
but continuing decreasing trend.
Indices based on nitrogen transformations can be another important group of
indicators of compost maturity. One of the most important indices is the ratio
N-NH4+/N-NO3– which defines the rate of transformation of the ammonium form of
nitrogen into the nitrate form, with relation to the conditions in the prism. It is assumed
that a value of the ratio of N-NH4+/N-NO3– close to 1 indicates the beginning of
stabilisation of processes related to nitrogen transformation, characteristic for mature
compost. In the analysed composts (Table 2), distinct stabilisation of that index was
504
Jakub Bekier et al
observed in the case of Zielona Gora after 107 days of composting, when its value was
less than 0.2. Modifications applied in the maintenance of the prism in Katowice
resulted in slower rate of transformation of nitrogen compounds, which was evidenced
by a higher value of that index (above 1.0) after 180 days of composting. Based on the
index N-NH4+/N-NO3–, the compost produced in Katowice did not reach full maturity
even after such a long time of composting.
Another index defining the maturity of composts on the basis of nitrogen transformations is the percentage share of its water-soluble forms in relation to the total
nitrogen content (Nw/Nt) × 100. In both composts under study stabilisation of this index
was observed after 90–107 days of composting, and its value oscillated within the range
of 8.8–5.3 % in Zielona Gora, and 7.1–4.6 % in Katowice (Table 2).
Analyses of the composts from Katowice and Zielona Gora showed changes in
the value of the index of mineralisation of nitrogen extracted in water extract
(Nmin/Nw) × 100. In both composts (Table 2) an increase was observed in the value of
that index with the passage of time of composting, with stabilisation after 127 days. The
less favourable aerobic conditions and the extended thermophilic phase during
composting in Katowice resulted in a certain modification of the values of the index.
Based on the calculated coefficients of correlation between the composting conditions (time, temperature and moisture) and the amount of organic carbon and nitrogen
forms, matrices of correlation were created (Table 3). In both composts significant
negative correlation was found between the content of Corg and temperature and time of
composting, and significant positive correlation between organic carbon level and
moisture. The parameter that distinctly differentiated nitrogen transformations in the
composts was temperature. The levels of Nt and N-NO3– displayed significant positive
correlation with composting time and temperature, while the amounts of water-soluble
nitrogen Nw were significantly negatively correlated with those parameters. In the case
of the compost from Zielona Gora, significant negative correlation was found between
the run of composting temperature and time and the amount for created forms N-NH4+,
while in the compost from Katowice temperature did not have any significant effect on
the level of those forms.
Table 3
Correlation coefficients between composting parameters and organic carbon
and different forms of nitrogen
Parameters
Composting time
Temperature
Humidity
Corg
–0.87
–0.97
–0.82
Nt
Nw
Katowice (N = 33, p < 0.05)
–0.92
–0.76
–0.75
–0.79
–0.50
–0.73
N-NH4+
N-NO3–
–0.64*
–0.33*
–0.09*
–0.56*
–0.62*
–0.27*
–0.78*
–0.49*
–0.34*
–0.96*
–0.54*
–0.53*
Zielona Gora (N = 30, p < 0.05)
Composting time
Temperature
Humidity
–0.76
–0.94
–0.62
* Non – significant correlation.
–0.93
–0.58
–0.52
–0.88
–0.74
–0.63
505
Significant positive correlation between moisture and content of Nw, determined in
both composts, indicates an increase in the content of that form of nitrogen with
moisture. Negative correlation between moisture and the content of Nt in both composts
may indicate unfavourable effect of increased moisture on nitrogen content in the
compost. Also noteworthy is the discovery of significant negative correlation between
moisture and the content of N-NO3– that occurred in the compost from Zielona Gora.
This relationship indicates that increase in moisture may result in decrease in the
content of that form of nitrogen in composted material. In the compost from Katowice
no significant correlation was found between moisture and the content of N-NH4+ and
N-NO3–. This may be grounds for conclusion that composting technology may have
a strong effect on nitrogen forms occurring in composts.
Conclusions
1. During composting of solid municipal wastes a decrease was observed in the
content of organic carbon, an increase in the total content of nitrogen, and quantitative
changes in the levels of particular forms of nitrogen.
2. The rate of nitrogen transformations depended primarily on compost moisture, on
the time of composting, and on the composting technology applied.
3. During compost maturation there was an increase in the content of N-NO3–, and
the intensity of that process was inhibited under less favourable aerobic conditions.
4. The study shows that the index N-NH4+/N-NO3– provides good representation of
nitrogen transformations in the course of composting and can be applied for the
estimation of compost maturity.
References
[1]
[2]
[3]
[4]
[5]
[6]
[7]
[8]
[9]
Morisaki N., Phae C. G., Akasaki K., Shoda M. and Kubota H.: J. Form. Bioen. 1989, 67, 57–61.
Drozd J. and Licznar M.: Acta Agrophys. 2002, 70, 117–126.
Chanyasak V. and Kubota H.: J. Ferment, Technol. 1981, 50(3), 215–219.
Drozd J. and Licznar M.: Zesz. Probl. Post. Nauk Roln. 2003, (493), 749–758.
Drozd J., Licznar M., Patorczyk-Pytlik B. and Rabikowska B.: Zesz. Probl. Post. Nauk Roln. 1996,
(437), 123–130.
Drozd J. and Licznar M.: Przemiany form azotu w procesie kompostowania odpadów komunalnych
w ró¿nych warunkach uwilgotnienia i przy ró¿nym dodatku mocznika, [in:] Komposty z odpadów
komunalnych – produkcja wykorzystanie i ich wp³yw na œrodowisko, Drozd J. (ed.), PTSH, Wroc³aw
2004, 141–150.
Chang J. I., Tsai J. J. and Wu K. H.: Bioresour. Technol. 2006, 97, 116–122.
Jimenez E. I. and Garcia V. P.: Agricult., Ecosyst. Environ. 1992, 38, 331–343.
Castaldi P., Alberti G., Merella R. and Melis P.: Waste Manage. 2005, 25, 209–213.
PRZEMIANY ZWI¥ZKÓW AZOTU W KOMPOSTACH
PRODUKOWANYCH ZE STA£YCH ODPADÓW MIEJSKICH
Instytut Nauk o Glebie i Ochrony Œrodowiska
Uniwersytet Przyrodniczy we Wroc³awiu
Abstrakt: Celem przeprowadzonych badañ by³o okreœlenie kierunków i intensywnoœci procesów transformacji azotu w kompostach produkowanych z odpadów miejskich z uwzglêdnieniem czasu i warunków
506
Jakub Bekier et al
kompostowania oraz zastosowanej technologii. Badaniami objêto komposty wytwarzane z odpadów miejskich
wed³ug odmiennych technologii: MUT-DANO w Katowicach i KKO-100 w Zielonej Górze. W celu poznania
warunków procesów przemian azotu, wykonano oznaczenia: temperatury, wilgotnoœci aktualnej, pH w KCl,
Corg – wêgla organicznego, Nog – azotu ogó³em, Nw – azotu wodnorozpuszczalnego (kompost: woda jak 1:10),
N-NH4+ i N-NO3– w ekstraktach wodnych (1:10). Wyniki badañ wykaza³y, i¿ w czasie kompostowania
odpadów miejskich nastêpuje wzrost zawartoœci Nog i N-NO3– oraz obni¿enie zawartoœci Nw i N-NH4+.
Intensywnoœæ tych zmian, zale¿a³a od warunków kompostowania. Przed³u¿one warunki beztlenowe w materiale kompostowanym w Katowicach, hamowa³y procesy nitryfikacji, co wyra¿a³o siê zmniejszeniem iloœci
formy N-NO3– w stosunku do N-NH4+. Bior¹c pod uwagê indeks N-NH4+/N-NO3–, kompost produkowany
w Katowicach nie osi¹gn¹³ stanu pe³nej dojrza³oœci nawet po 180 dniach kompostowania.
S³owa kluczowe: kompostowanie odpadów miejskich, transformacja azotu
A
Vol. 18, No. 4
2011
Jacek CZEKA£A1
INFLUENCE OF LONG-TERM SPRINKLING IRRIGATION
AND NITROGEN FERTILISATION
ON SOIL NITROGEN CONTENT
OF A CEREAL CROP ROTATION
WP£YW WIELOLETNIEGO DESZCZOWANIA
I NAWO¯ENIA AZOTEM NA ZAWARTOŒÆ AZOTU
W GLEBIE P£ODOZMIANU ZBO¯OWEGO
Abstract: The paper presents results of investigations on the proportion contents of different nitrogen forms
in the soil in conditions of a long-term cereal crop rotation. The experimental factors included sprinkling
irrigation and nitrogen applied at various doses. It was found, among others, that the sprinkling irrigation
failed to influence the content of the examined nitrogen forms in contrast to the nitrogen impact whose effect
was statistically significant. A synergistic influence of both factors became apparent only in the case of the
content of easily-hydrolysable nitrogen (N-EH).
Keywords: soil, cereal crop rotation, nitrogen forms, fertilisation
Nitrogen occurs in soils in various forms of which organic bonds prevail [1, 2]
which, at the humic levels of soils, make up from 93 to 99 % of total nitrogen [3]. It is
evident from investigations [4] that at least half of the content of nitrogen in soils is
described as ‘unknown nitrogen’ which undergoes hydrolysis only to a very limited
extent. It is very likely that this nitrogen is strongly bound with humins. However,
nitrogen occurs also in the structures of humic and fulvic acids whose quantity and
durability of bonds depend, among others, on the size of molecules [5]. The structure of
these bonds is important from the point of view of the availability of the component to
plants whose transformations in soils run along a complex circulation and in two cycles:
internal and external. They take place simultaneously with organic matter changes due
to their common microbiological character [6]. For this reason, properties of the organic
matter introduced into the soil – primarily, the C:N ratio – exert a strong influence on
1
Department of Soil Science, University of Life Sciences in Poznan, ul. Szyd³owska 50, 60–656 Poznañ,
Poland, phone: +48 61 846 67 10, email: [email protected]
508
Jacek Czeka³a
the rate and directions of nitrogen compound transformations. In addition, this is also
associated with the quantity of after harvest residues of plants characterised by varying
amounts of carbon and nitrogen contents [7]. On the other hand, root bulk is
determined, by fertilisation, mainly with nitrogen, and soil moisture content [8].
Activities of these factors, as well as properties of the soil itself, ultimately influence
not only the dynamics of changes of nitrogen mineral forms [9, 10] but also other soil
properties [11].
It is quite probable, that in under long-term conditions, a unique equilibrium
develops between individual nitrogen forms which is a resultant of interactions between
the above-mentioned factors.
This paper presents the results of long-term field experiments involving the impact of
sprinkling irrigation and nitrogen fertilisation on soil nitrogen forms in conditions of
a cereal crop rotation system.
The analyses were carried out on soil samples derived from a long-term field
experiment situated in Zlotniki Experimental Station near Poznan (52o29’ latitude and
16o50’ longitude) which belongs to the Department of Soil and Plant Husbandry of
Poznan University of Life Sciences. The field trial was established accordingly to a
random schedule on a lessive soil classified as Albic Luvisols [12] developed from
loamy sands underlained mostly at 40–60 cm depth. The soil on the humus horizon
(0–25 cm) was characterised by 13–14 % content of fraction with < 0.02 mm diameter,
including 3 to 4 % clay (< 0.002 mm) and pH(KCl) in the range 5.7 to 6.5. Soil samples
were collected from the humus horizon following 26-year long-term cereal rotation
experiment in which the following crop plants were grown: winter wheat, spring
triticale, spring barley, and oat.
The first degree factor was sprinkling irrigation (sprinkle-irrigated objects – S and
objects without sprinkling – NS) and the second degree factor – nitrogen fertilisation in
different doses. The mean annual doses per crop rotation comprised [kg × ha–1]:
N0 – 0.0; N1 – 50.0; N2 – 100.0; N3 – 150.0. Mean doses of phosphorus (P) amounted to
35.0 kg × ha–1 and potassium (K) – 83.0 kg × ha–1.
The employed cereal crop rotation system began with wheat which was fertilised in
the case of each rotation series with farmyard manures in the amount of 30 Mg × ha–1.
All treatments were performed in four replications.
After drying and trituration, the soil material was screened through a sieve with
2 mm sieve mesh and results were expressed on a dry weight basis.
The following nitrogen fractions were isolated with the assistance of sequential
analysis:
– Water soluble and exchangeable nitrogen (inorganic N-inorg.) following soil
shaking in 1 M NaCl solution for 2 hours; soil:solution – 1:5. The entire material was
centrifuged and filtered into 100 cm3 volume measuring flasks. Mineral N in samples
Influence of Long-Term Sprinkling Irrigation and Nitrogen Fertilisation...
509
was determined by the distillation method of Bremner [13] with MgO added for
ammonium distillation followed by the addition of Devard alloy nitrate.
– Easily-hydrolysable nitrogen (NEH) using 0.25 M solution of H2SO4. The soil was
hydrolysed at 1:5 ratio for 3 hours in a water bath at the temperature of 60 oC,
centrifuged and the solution was filtered into 250 cm3 volume measuring flasks. The
residue was washed twice with hot distilled water and the filtrate after centrifugation
was transferred into measuring flasks with acid extract.
– Poorly-hydrolysable nitrogen (N-PH) using 2.50 M solution of H2SO4. The soil
was hydrolysed at 1:5 ratio for 3 hours in a water bath at the temperature of 60 oC,
centrifuged and the solution was filtered into 250 cm3 volume measuring flasks. The
residue was washed twice with hot distilled water and the filtrate after centrifugation
was transferred into measuring flasks with acid extract.
– Non-hydrolysable nitrogen (NNH) – it was calculated from the difference between
the total nitrogen of soil (TN) content and the sum of isolated three fractions.
Total soil nitrogen (TSN) as well as the nitrogen of fractions (TNF) were determined
by the Kjeldahl method using for this purpose 2300 Kjeltac Analyzer Unit apparatus.
Results were expressed in mg × kg–1 dry weight and subjected to the analysis of
variance (STAT) using Duncan test for parametric evaluation at the significance level of
p £ 0.05.
Transformations of soil nitrogen compounds run simultaneously with organic matter
transformations. The dynamics of these transformations taking place within the
framework of mineralisation and humification processes preconditions, among others,
nitrogen availability to plants. Nevertheless, the rate of the occurring processes varies
and depends on many factors. In the performed fertilisation trials [14], it was
demonstrated that nitrogen and the type of the soil complex were among factors
differentiating the content of mineral forms of nitrogen in the soil. According to
Dechnik and Wiater [15], factors which influenced the dynamics of nitrate nitrogen(V)
changes in the soil comprised: atmospheric conditions and, to a lesser extent, the type of
the applied fertilisation. However, nitrogen introduced into the soil, irrespective of the
form and source, always undergoes transformation into different forms, not only
mineral ones [16].
The results collated in Table 1 concerning the distribution of nitrogen in soil samples
comprising the entire long-term period during which both experimental factors were
present revealed that the water factor (irrespective of the nitrogen fertilisation) did not
exert a significant influence on the amount of the examined nitrogen forms in the soil.
On the other hand, mineral nitrogen applied at various doses, irrespective of the applied
sprinkling irrigation (Table 1) – with the exception of non-hydrolysable nitrogen forms
(NNH) and total nitrogen – exhibited a significant impact as confirmed by mean
nitrogen contents found in one uniform group (a).
510
Jacek Czeka³a
Table 1
Independent impact of sprinkler irrigation and nitrogen fertilisation on the content
of nitrogen forms in soil
Factor
Nitrogen of forms [mg × kg–1]
Nmin1
NEH2
NDH3
NNH4
Total
S
37.10a
102.83a
247.20a
304.45a
691.67a
NS
35.06a
101.44a
244.99a
321.01a
702.50a
0.19
0.13
0.03
0.12
0.08
Test E, p < 0.05
Nitrogen dosses
N0
26.60a
101.23a
284.38c
247.79a
660.00a
N1
31.85ab
95.68a
258.67bc
328.80
715.00a
N2
40.95ab
98.62a
200.67a
358.09a
698.33a
N3
44.92b
113.02b
240.85b
316.21a
715.00a
3.18*
4.02*
8.05*
1.04*
Test E, p < 0.05
0.46
1
– Nmin (Inorganic) N; 2 – Easily hydrolysable N; 3 – Difficulty hydrolysable N; 4 – Non-hydrolysable N;
* significant at p < 0.05.
The impact of the cooperation of the water factor with nitrogen also turned out to be
small and, practically speaking, became apparent only with regard to the influence of
easily-hydrolysable nitrogen content (Table 2). It is clear from the statistical evaluation
utilising the uniform group parameter that the highest significant effect of experimental
factors was observed in the case of easily-hydrolysable forms of nitrogen. However, no
unequivocal direction of NEH quantitative changes were observed depending on the
activity of these factors. Nevertheless, in the treatment with sprinkling irrigation, mean
quantities of these nitrogen forms increased with N doses. This increase between the
control treatment without nitrogen (N0) and the N3 dose amounted to 25.2 %. On the
other hand, in the treatment without sprinkling, NEH quantities between the discussed
nitrogen doses remained on a similar level. What was puzzling was the recorded
absence of statistically significant differences between the experimental treatments with
non-hydrolysable nitrogen (NNH) forms, despite quantitative differences found between
treatments (Table 2).
However, it should be emphasised that higher nitrogen doses in conditions of
increased moisture favoured the accumulation of the N-NH form in the soil. At average
nitrogen doses of the order of 100 and 150 kg × ha–1 during the period of 26 years of the
experiment, the content of the non-hydrolysable nitrogen on these objects amounted to
377.0 and 346.1 mg × kg–1, respectively, while on objects without sprinkling irrigation –
339.3 and 283.7 mg × kg–1.
The content configuration of individual nitrogen forms determined in this study
indicates a relatively high stability of mineralisation and humification processes in the
soil, especially, in view of the fact that according to some researchers [17, 18] all
combinations of this element – including the non-hydrolysable ones – take part in
processes of soil nitrogen transformations. Most nitrogen from this group has not been
identified so far and the recognised forms indicate their heterocyclic structure [18].
511
Table 2
Impact of the cooperation of experimental factors on the content of nitrogen forms
in soil humus horizon [mg × kg–1]
Water factor
S
NS
Nitrogen forms
Nitrogen fertilization
N0
N1
N2
N3
N0
N1
N2
N3
Nmin
26.8
30.7
49.0
32.0
16.2
32.4
32.8
50.5
NEH
89.9ab
107.3cd
101.5bcd
112.6cd
84.0a
95.7abc
113.4d
NDH
274.2b
279.9b
294.6b
237.4ab
208.8a
239.1ab
269.9a
389.1a
339.3a
283.7a
703.3a
743.3a
676.7a
743.3a
433.5c
354.2ab
337.3a
403.0abc
60.2
47.6
49.8
59.7
Test F, p < 0.05–1.08
112.6cd
Test F, p < 0.05–6.30
192.5a
242.6ab
Test F, p < 0.05–1.35
NNH
225.8a
268.8a
377.0a
346.1a
Test F, p < 0.05–0.82
NT
616.7a
686.7a
720.0a
743.3a
Test F, p < 0.05–2.74
N-Sol*
390.9abc
417.9bc
343.0a
397.4abc
Test F, p < 0.05–1.08
N-Sol in total [%]
63.4
60.9
47.6
52.1
* Sum of soluble nitrogen (N-Sol).
From the point of view of nitrogen availability for plants, easily soluble nitrogen
fractions, whose dynamics affect the release of mineral bonds of this element, are the
most important. The cooperation of the water and nitrogen factors in the NEH content
testifies to the sensitivity of these bonds to soil transformations. It is quite probable that
they affect mainly amides, a certain quantity of amines as well as part of the
non-exchangeable nitrogen. Although their proportion in total nitrogen ranged only
from 11.4 to 16.7 %, this form was characterised by a relatively high stability,
irrespective of experimental factors (Fig. 1). Especially, that in the case of poorly-hydrolysable forms, the author observed a decrease in their proportions in total N in
conditions of sprinkling and higher nitrogen doses. Without N fertilisation, this
proportion amounted to 44.5 % in conditions of sprinkling irrigation, 41.9 % without
sprinkling, while at the highest N dose – 32.6 and 35.3 % respectively. It is, however,
more important that the highest drop in the proportion of this nitrogen form occurred at
the average nitrogen dose of 100 kg × ha–1. This proportion amounted to only 26.7 % in
the case of the sprinkling irrigation treatment and to 30.9 % – for the non-irrigated one.
However, this high decline in the discussed proportion was not only the result of losses
of this constituent but also of its transformations to non-hydrolysable forms which in the
case of these treatments amounted to 52.4 % and 50.2 % (Fig. 1), respectively.
512
Jacek Czeka³a
N0
N0
N1
N1
N2
N2
N3
N3
[%] 100
N-inorg.
NEH
80
NDH
NNH
60
40
20
0
S
NS
S
NS
S
NS
S
NS
Fig. 1. Percentage share of nitrogen forms in soil as effected by sprinkling irrigation and nitrogen
fertilization
Therefore in conditions of long-term cultivation of cereal plants alone a dynamic
equilibrium developed between nitrogen forms on which the sprinkling level failed to
exert a significant impact. Mineral nitrogen applied at doses of 100 kg × ha–1, together
with after-harvest residues as well as the plant root bulk, ensured optimal conditions for
the formation of non-soluble nitrogen forms on the one hand and, on the other, soluble
forms, potentially available for plants.
Conclusions
1. Sprinkling irrigation did not exert a significant influence on the content of
investigated N forms in the soils, under experimental conditions.
2. Nitrogen fertilization significantly differentiated the contents of N mineral forms,
easily and poorly hydrolysable N. In the case of total N as well as non-hydrolysable any
influence was not observed.
3. Elevated nitrogen doses caused a significant increase of mean concentrations of
the mineral forms of the element in the soil as well as significant differences in easilyand poorly-hydrolysable nitrogen but without unequivocal direction of changes.
4. A synergistic effect of sprinkling irrigation and nitrogen manifested its significant
impact only with regard to the development of easily-hydrolysable nitrogen forms.
5. No unequivocal trend in changes of N fractions as induced by the water factor and
nitrogen fertilization were revealed under conditions of the current field trial.
References
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[2] Stevenson F.J.: Humus chemistry. Genesis, composition, reactions. John Wiley & Sons, New York 1982,
13–52.
[3] Orlov D.C.: Khimja poczv. Izd. Moskov. Univer., Moskva 1985, 281–291.
[4] Schnitzer M., Marshall P.R. and Hinde D.A.: Canad. J. Soil Sci. 1983, 63(3), 425–433
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[5] Go³êbiowska D.: Rola organicznych zwi¹zków azotu w procesie humifikacji. Powstawanie i biotransformacja po³¹czeñ azotowo-fenolowych, AR Szczecin, Rozprawy 1982, 82, pp. 300.
[6] £oginow W., Andrzejewski J., Wiœniewski W., Kusiñska A., Cieœliñska B., Karlik B. and Janowiak J.:
Wp³yw monokulturowej uprawy zbó¿ na przemiany materii organicznej i azotu w glebie, [in:]
Ekologiczne procesy w monokulturowych uprawach zbó¿ Ryszkowski L., Karg J. and Pude³ko J. (eds.).
Wyd. UAM, Poznañ 1990, 111–125.
[7] Rimovsky K.: Acta Acad. Agricult. Techn. Olst. 1987, 44, 163–170.
[8] Czeka³a J., Szuka³a J. and Jakubus M.: Zesz. Probl. Post. Nauk Roln. 2003, 494, 77–84.
[9] Czeka³a J.: Chem. Agric. 2004, 5, 266–271.
[10] Koæmit A., Tomaszewicz T., Raczkowski B., Chudecka J., Podlasiñski M. and Skokowska-Antoszek M.:
Zesz. Probl. Post. Nauk Roln. 1996, 438(3), 325–338.
[11] Czeka³a J.: Zesz. Prob. Post. Nauk Roln. 2002, 482, 99–105.
[12] IUSS Working Group WRB. Word reference base for soil resources 2006. Word soil Resources Reports
No. 103, 2007, FAO, Roma.
[13] Bremner J.M.: Inorganic forms of nitrogen, [in:] Methods of soil analysis. C.A. Black (ed.) Part 2,
Agronomy 1965, 9, 1179–1237. Amer. Sci. Soc. Agr. Inc., Madison, USA.
[14] Cieæko Z., Wyszkowski M. and Szaga³a J.: Zesz. Probl. Post. Nauk Roln. 1996, 440, 27–33.
[15] Dechnik I. and Wiater J.: Zesz. Probl. Post. Nauk Roln. 1996, 440, 75–80.
[16] Andrzejewski M. and Czeka³a J.: PTPN, Pr. Komit. Nauk Roln. i Kom. Nauk Leœn., Poznañ 1981, LI,
7–17.
[17] Ashok A., Siva P. and Kennth S.: Arch. Agron. Soil Sci. 2006, 52(3), 321–332.
[18] Fleige H., Meyer B. and Schulz H.: Göttinger Bodenk 1971, 18, 39–86.
WP£YW WIELOLETNIEGO DESZCZOWANIA I NAWO¯ENIA AZOTEM
NA ZAWARTOŒÆ AZOTU W GLEBIE P£ODOZMIANU ZBO¯OWEGO
Katedra Gleboznawstwa i Ochrony Gruntów
Uniwersytet Przyrodniczy w Poznaniu
Abstrakt: Przedstawiono wyniki dotycz¹ce zawartoœci udzia³u ró¿nych form azotu w glebie ukszta³towane
w warunkach wieloletniej uprawy w p³odozmianie zbo¿owym. Czynnikami doœwiadczenia by³o deszczowanie
i azot stosowany w ró¿nych dawkach. Stwierdzono miêdzy innymi, ¿e deszczowanie nie mia³o wp³ywu na
zawartoœæ badanych form N, w odró¿nieniu od dzia³ania azotu, którego dzia³anie by³o statystycznie istotne.
Wspó³dzia³anie obu czynników ujawni³o siê tylko w kszta³towaniu zawartoœci azotu ³atwo hydrolizuj¹cego.
S³owa kluczowe: gleba, p³odozmian zbo¿owy, formy azotu, nawo¿enie, deszczowanie
A
Vol. 18, No. 4
2011
Franciszek CZY¯YK1 and Agnieszka RAJMUND1
QUANTITY OF NITROGEN DEPOSITED IN SOIL
AS PRECIPITATED FROM ATMOSPHERE
IN THE WROCLAW AREA DURING 2002–2007
ILOŒÆ AZOTU WNOSZONA DO GLEBY
Z OPADAMI ATMOSFERYCZNYMI W REJONIE WROC£AWIA
W LATACH 2002–2007
Abstract: Nitrogen content was examined in total atmospheric precipitation in eastern outskirts of Wroclaw.
Overall nitrogen content varied considerably and ranged from 0.8 to 16.8 mg N × dm–3. Of substantial
proportion in overall nitrogen was nitrate (V) nitrogen whose concentration in atmospheric precipitations
ranged from 0.3 to 3.7 mg N × dm–3. Also of diversity were both monthly as well as annual charges of
nitrogen deposited in the soil along with precipitations. Annual charges of nitrogen deposited in the soil
amounted from 33 to 42 kg N · ha–1, and average multiyear charge amounted to 37.8 kg N · ha–1, of which
over 60 % can be assigned to growing season. These are quantities that should be taken into consideration in
fertilization balance of agricultural farming.
Keywords: atmospheric precipitation, total nitrogen, nitrates
Nitrogen content as precipitated from atmosphere remains in strict correlation with
air pollution and directions of its flow. Pollution of atmospheric precipitation with
nitrogen compounds therefore depends on intensity of emission of these components
from various sources and location of examination site with respect to such sources, as
well as direction of flow of atmospheric air mass. Precipitations, participating in cycle
of water and elements in nature, constitute among others the carrier of nitrogen.
Through physical and chemical processes, they absorb nitrogen contained in atmospheric air pollution and carry it into the soil along with water.
The purpose of the paper presented is to examine the chemical composition of total
atmospheric precipitation and to obtain data for balance of nitrogen, which is carried
into the soil.
1
Institute of Technology and Life Sciences – Lower Silesia Research Centre in Wroc³aw, ul. Z. Berlinga 7, 51–209 Wroc³aw, Poland, phone/fax: +48 71 367 80 92, email: [email protected], [email protected]
516
Franciszek Czy¿yk and Agnieszka Rajmund
The studies presented were conducted at the research centre of Institute of Land
Reclamation and Grassland Farming (IMUZ), situated in the eastern outskirts of
Wroclaw. Dominating in the place of measuring quantities of precipitation and
sampling for examinations are westerly winds, displacing air mass mainly from the city
area. Quantities of atmospheric precipitations were measured using the Hellman
rain-gauge. In order to obtain sufficient volume of samples for laboratory analyses,
additional precipitation was collected into vessels of increased surface area (approx.
0.3 m2). Total precipitation was collected and examined, and hence wet precipitation
along with the so-called dry precipitation. Samples for testing were taken after each
precipitation and delivered immediately after drawing to the laboratory where, determined among others, was the content of total Kjeldahl nitrogen (colorimetrically,
after mineralization according to Kjeldahl) and nitrate(V) nitrogen – colorimetrically,
after the Devarde reaction [1, 2].
Results and discussions
Quantities of atmospheric precipitations, both monthly as well as yearly, were very
diverse (Table 1). In general, it can be stated that in the first three years of studies,
precipitations were lower than average multiyear precipitations for the Wroclaw region
and higher in the subsequent three years. Also diverse were concentrations of total
nitrogen as well as nitrate(V) nitrogen in atmospheric precipitations (Table 2).
Dependence of nitrogen concentration in precipitations on their amounts cannot
however be ascertained. Since nitrogen in atmospheric precipitations originates from
numerous sources both natural as well as anthropogenic, and its quantity depends on
intensity of emissions from these sources.
Contents (concentrations) of total nitrogen in atmospheric precipitations presented in
Table 2 fluctuate from 3.2 to 16.8 mg N × dm–3, and of nitrate(V) nitrogen from 0.3 to
4.0 mg N × dm–3. On the basis of these contents and amounts of precipitations, charges
of nitrogen carried into the soil along with the precipitations were calculated (Table 3).
The results obtained showed large diversities in monthly charges of nitrogen carried
into the soil along with atmospheric precipitations. The largest charges occurred in the
spring and summer months, particularly in July and August. Average monthly charges
from the years 2002–2007, during the spring-summer half-year fluctuated from 1.78 to
6.43 kg N · ha–1, whereas during the autumn-winter period, they were more uniform and
amounted from 2.28 to 2.70 kg N · ha–1. Annual quantity of nitrogen carried into the soil
fluctuated from 33.6 to 42.8 kg N · ha–1, of which during the spring-summer half-year, it
amounted to 58–65 % of total quantity. The increased concentration of nitrogen in
atmospheric precipitations during the spring-summer period and its significantly larger
deposition into the soil in comparison with the autumn-winter period may result from
several causes. During the spring-summer period, increased emission of gaseous
nitrogen compounds occurs, originating in biochemical processes of mineralization of
organic substances in the soil and on its surface. Also occurring in this period, there is
23.8
40.0
31.2
46.2
28.9
64.6
2003
2004
2005
2006
2007
I
2002
Year
53.3
43.7
51.2
60.6
2.8
59.2
II
55.5
26.1
11.5
56.6
18.7
15.7
III
3.6
54.2
27.0
24.5
11.9
32.9
IV
57.6
21.9
150.8
35.2
80.5
37.1
V
79.5
56.6
46.8
40.5
24.3
68.2
VI
124.1
12.0
122.6
88.5
58.8
49.5
VII
42.0
179.3
54.4
50.8
55.3
78.7
VIII
Months and precipitations [mm]
51.6
20.3
24.9
21.8
42.4
52.2
IX
26.5
68.4
6.7
45.6
51.5
61.2
X
Precipitations at Research Station in Kamieniec Wroclawski in the years 2002–2007\
56.0
65.6
31.0
81.4
27.8
52.3
XI
27.9
36.7
106.4
15.4
47.3
16.2
XII
642.0
613.7
679.5
552.1
461.5
547.0
Annual
precipitation
[mm]
Table 1
Quantity of nitrogen deposited in soil as precipitated from atmosphere...
517
0.86
N-NO3
1.00
0.8
6.14
0.8
N-NO3
5.58
4.7
5.4
Ntot
Ntot
1.2
5.0
1.0
5.0
Ntot
N-NO3
0.8
0.9
5.2
5.0
N-NO3
1.4
0.8
Ntot
6.8
6.1
Ntot
N-NO3
0.8
9.0
0.8
6.4
Ntot
N-NO3
—*
—*
—*
—*
II
I
N-NO3
Ntot
Nitrogen
form
* – lack of measurement.
Average
for period
2002–2007
2007
2006
2005
2004
2003
2002
Year
1.94
7.74
0.3
3.2
0.8
2.1
2.0
9.4
2.8
8.6
2.5
9.5
—*
—*
III
1.28
7.28
1.4
7.4
1.3
5.2
0.8
9.2
2.2
8.5
0.9
6.8
1.1
6.6
IV
1.42
7.17
1.3
5.6
1.2
5.2
1.2
5.5
2.8
9.7
1.2
8.1
0.8
8.9
V
1.72
6.37
0.8
5.0
1.7
5.1
0.7
5.4
3.7
7.8
1.1
7.3
2.3
7.6
VI
1.55
10.37
0.7
6.2
3.0
16.8
1.0
5.3
1.2
11.4
1.4
12.4
2.0
10.1
VII
1.68
7.80
0.7
4.7
1.4
6.0
0.8
4.9
4.0
10.0
1.8
9.9
1.4
11.3
VIII
1.60
6.42
1.7
6.3
2.1
6.9
1.6
6.0
1.1
5.6
1.7
7.0
1.4
6.7
IX
Monthly and mean weighed content of nitrogen [mg N × dm–3]
Contents of total nitrogen and nitrate(V) nitrogen in precipitations in the years 2002–2007
0.97
5.95
1.2
5.8
0.6
3.7
1.0
5.7
1.4
6.4
0.5
6.0
1.1
8.1
X
1.38
5.58
0.9
5.4
0.6
3.8
1.2
5.9
1.4
3.8
3.3
7.5
0.9
7.1
XI
0.88
6.06
0.9
5.3
0.5
5.0
0.6
4.9
1.0
6.6
1.4
7.7
0.9
6.9
XII
Table 2
518
2.18
2.50
1.90
2.31
1.44
3.49
2.34
2004
2005
2006
2007
Average
for years
2002–2007
—
2.28
1.77
2.08
1.08
4.86
1.60
—
III
1.78
0.33
2.82
2.48
2.08
0.80
2.17
IV
4.31
3.22
1.14
8.29
3.41
6.52
3.30
V
3.25
3.97
2.89
2.53
3.16
1.77
5.18
VI
6.43
7.69
2.02
6.50
10.1
7.29
5.00
VII
5.80
1.97
10.76
2.67
5.08
5.47
8.90
VIII
Month and nitrogen charge [kg N · ha–1]
** Nitrogen charge in period IV–XII; ** average for years 2003–2007.
2.34
2.66
4.12
0.25
—
2.56
II
2003
I
2002
Year
2.31
3.25
1.40
1.50
1.22
2.97
3.50
IX
2.53
1.54
2.53
0.40
2.74
3.09
4.90
X
2.70
3.02
2.49
1.83
3.09
2.08
3.71
XI
2.38
1.45
1.84
5.21
1.02
3.64
1.12
XII
24.4
23.5
21.0
24.0
25.1
24.8
28.0
14.15**
13.8
12.6
13.5
17.7
13.2
—
37.83**
37.3
33.6
37.5
42.8
38.0
37.8*
Period
Period
Year
IV–IX
X–III
kg N · ha–1
–1
kg N · ha
kg N · ha–1
Monthly periodical and annual nitrogen charge deposited in the soil with precipitation
Table 3
519
520
much more pollution of air with organic dust (eg plant pollen) and there is larger
absorption of gaseous nitrogen compounds by rainwater than by snow in winter. The
studies of Burszta-Adamiak and Stodolak [3] showed that concentrations of ammonia
nitrogen and nitrates in rainwater were significantly larger than in snow.
In spring and summer, intensification of motor transport emitting nitrogen oxide, is
also considerably larger than in winter. At present, apart from electric power plants and
also heat and power generating plants, the largest source of nitrogen oxides in the air
and hence also in atmospheric precipitations, is motor transport. According to
Zakrzewski [4], nitrogen oxides form 45 % of total quantity of atmosphere pollutions in
large towns.
The quantity of nitrogen carried into the soil from atmospheric precipitations in the
region of Wroclaw is comparable with the charge given by Sapek [5] deposited in
Central Europe, exceeding 30 kgN · ha–1 · year–1. Charges of nitrogen deposited in the
soil on the outskirts of Wroclaw however were considerably higher than in some
regions of Poland. According to relevant literature, charges in southern vicinities of
Warsaw, or also in the region of Ostroleka amount to about 18 kg N · ha–1 · year–1
[6, 7], and in south-eastern parts of Pomerania – from 16 to 26 kg N · ha–1 · year–1 [8].
In these regions however, there is lesser pollution of air, eg annual emission of nitrogen
oxides in the year 2007 amounted there to 500–1200 Mg, and in Wroclaw to 2700 Mg [9].
Conclusions
1. Annual quantity of nitrogen deposited in the soil from atmospheric precipitation in
the region of large, industrialized urban area as is Wroclaw, is high and ranges from 33
to 42 kg N · ha–1, and average multiyear charge amounted to 37.8 kg N · ha–1.
2. More than 60 % of annual nitrogen charge is deposited in the soil with
atmospheric precipitation during growing season. The largest monthly charges of
nitrogen occur in July and August.
3. Quantities of nitrogen deposited in the soil with atmospheric precipitation are
significant for fertility of soil and should be taken into consideration in the fertilization
balance of ecological, agricultural farming particularly ecological farming producing
so-called health food.
References
[1] Hermanowicz W., Do¿añska W., Dojlido J., Koziorowski B. and Zerbe J.: Fizyczno-chemiczne badania
wody i œcieków. Arkady, Warszawa 1999.
[2] Marzenko Z. and Balcerzak M.: Spektrofotometryczne metody w analizie nieorganicznej. PWN,
Warszawa 1998.
[3] Burszta-Adamiak E. and Stodolak R.: Woda – Œrodowisko – Obszary Wiejskie 2007, 7(20), 83–94.
[4] Zakrzewski S.: Podstawy toksykologii œrodowiska. PWN, Warszawa 2000.
[5] Sapek A. and Nawalany P.: Woda – Œrodowisko – Obszary Wiejskie 2004, 4(10), 177–182.
[6] Sapek A., Nawalany P. and Barszczewski J.: Woda – Œrodowisko – Obszary Wiejskie 2003, 3(6), 69–77.
[7] Sapek A. and Nawalany P.: Woda – Œrodowisko – Obszary Wiejskie 2006, 6(17), 23–27.
[8] Wicik B.: Prace i Studia Geograficzne Warszawa 2005, 36, 121–130.
[9] Ochrona Œrodowiska. GUS, Warszawa 2008.
521
ILOŒÆ AZOTU WNOSZONA DO GLEBY Z OPADAMI ATMOSFERYCZNYMI
W REJONIE WROC£AWIA W LATACH 2002–2007
Instytut Technologiczno-Przyrodniczy
Dolnoœl¹ski Oœrodek Badawczy we Wroc³awiu
Abstrakt: Badano zawartoœci azotu w ca³kowitych opadach atmosferycznych na wschodnim obrze¿u
Wroc³awia. Zawartoœci azotu ogólnego by³y bardzo zró¿nicowane i waha³y siê od 0,8 do 16,8 mg N × dm–3.
Znaczny udzia³ w azocie ca³kowitym mia³ azot azotanowy, którego stê¿enie w opadach atmosferycznych
waha³y siê od 0,3 do 3,7 mg N × dm–3. Zró¿nicowane by³y te¿, zarówno miesiêczne, jak i roczne ³adunki
azotu wniesionego do gleby z opadami. Roczne ³adunki azotu wniesionego do gleby wynosi³y od 33 do
42 kg N · ha–1, a œredni wieloletni ³adunek wynosi³ 37,8 kg N · ha–1, z czego ponad 60 % przypada na okres
wegetacyjny. S¹ to iloœci, które powinny byæ uwzglêdniane w bilansie nawozowym gospodarstw rolnych.
S³owa kluczowe: opad atmosferyczny, azot ogólny, azotany
A
Vol. 18, No. 4
2011
Tadeusz FILIPEK1 and Pawe³ HARASIM1
NITROGEN CONTENT
AND AMINOACIDS PROTEIN COMPOSITION
OF GRAIN OF WINTER WHEAT FOLIAR FERTILIZED
WITH UREA AND MICROELEMENTS FERTILIZERS
ZAWARTOŒÆ AZOTU I SK£AD AMINOKWASOWY
BIA£KA ZIARNA PSZENICY OZIMEJ
DOKARMIANEJ DOLISTNIE MOCZNIKIEM
I NAWOZAMI MIKROELEMENTOWYMI
Abstract: The field experiment was carried out over 2003–2005 on the lessive soil (Haplic Luvisols),
defective wheat complex, with a randomised block method in four random replications. The soil was
characterised with an acid reaction (pHKCl – 5.3) and a natural content of trace elements (characteristic for the
geochemical background). A Rywalka (class A) high quality variety of winter wheat was used as a test crop.
The aim of this study was to determine the influence of foliar feeding with urea and nickel chelate
EDTA-Ni(II) and Plonvit Z for the total nitrogen content and endogenous amino acid composition of winter
wheat grains. The differentiation of the total nitrogen content and amino acid composition of protein under the
influence of experimental factors proved to be statistically insignificant. Under the influence of EDTA-Ni, the
amount of endogenous amino acids and content of leucine and lysine in the protein increased, while reducing
the overall protein content.
Keywords: nitrogen, amino acids, winter wheat, foliar feeding, urea, micronutrients
Protein plays a key role in almost all biological processes. The basic structural units
of proteins are amino acids [1]. The human diet must contain not only a sufficient
amount of protein – about 0.8 g of protein per kilogram of body mass – but the protein
must be of the appropriate type. The human organism is not able to synthesize the nine
basic amino acids (exogenous); therefore, it must be supplied additionally to the diet [2,
3]. The organism may produce certain amino acids (endogenous amino acids), such as
in the case of cystine, which are the main building blocks of hair. However, the amounts
that the human organism can produce are sometimes too low. Plants can synthesize all
amino acids; however, the majority of plant proteins show a deficit in one or more of
1
Departament of Agricultural and Environmental Chemistry, University of Life Sciences in Lublin,
ul. Akademicka 15, 20–950 Lublin. Poland, phone: +48 81 445 60 44; email: [email protected]
524
Tadeusz Filipek and Pawe³ Harasim
the basic amino acids, in the case of wheat it is the lysine amino acid that is limited.
Protein content and total amino acid composition may change depending on the species
of plants, variety, habitat, and fertilization [4].
In the preparation of feed mix, which is the bases for animal foodstuffs, cereals are
the most frequently used. The nutritional value of cereal proteins, which is largely
determined in the composition of amino acid, is a measure of the degree of utilisation of
proteins required for the synthesis of specific systemic proteins. Therefore, it is
important to strive for better use of not only protein, but for all nutrients so that it will
be possible to obtain physiological, economic, and environmental benefits [5].
Nickel was found as an essential elements for plants in 1987 [6], quite recently and in
1991 was rated in the group of micronutrients [7]. Its most important function is the
physiological activation of urease, which is so far the only known enzyme that contains
nickel [8]. Nitrogen contained in urea is not available in plants until the hydrolysis of
urea catalysed by urease to ammonia and carbon dioxide [9]. There are reports that the
addition of nickel can increase several times the activity of urease in the leaves [10, 11].
The aim of this study was to determine the influence of foliar feeding with urea and
nickel chelate EDTA-Ni(II) and Plonvit Z for the total nitrogen content and endogenous
amino acid composition of winter wheat grains.
Materials and methods
The field experiment was carried out over 2003–2005 on the lessive soil (Haplic
Luvisols), defective wheat complex, with a randomised block method in four random
replications. Size of plots: 6 × 5m = 30m2 gross, including 5,2 × 3m = 15,6m2 to
harvest.
The soil was characterised with an acid reaction (pHKCl – 5.3) and a natural content
of trace elements (characteristic for the geochemical background). A Rywalka (class A)
high quality variety of winter wheat was used as a test crop. The following fertilization
per one hectare was used: soil application per 1 ha: pre-sowing, 35 kg P in the form of
triple superphosphate and 120 kg K in the form of potassium salt, per capita before start
of vegetation 60 kg N in ammonium nitrate (solid form), and after vegetation started in
spring 60 kg N in the form of CO(NH2)2 (3 × 20 kg) by the experiment scheme (foliar
application). Deadlines of foliar feeding: I. height spring tillering (KD 25); II. stem
formation (KD 32) (2. node); III. beginning of ear formation (KD 51).
Experimental objects:
1. urea (3 × 20 kg N × ha–1) soil application in solid + MgSO4 × H2O + water
(spray 3×);
2. urea (3 × 20 kg N × ha–1) in a solution + MgSO4 × H2O;
3. urea (3 × 20 kg N × ha–1) in a solution + chelate nickel + MgSO4 × H2O;
4. urea (3 × 19.9 kg N × ha–1) in a solution + Plonvit Z + MgSO4 × H2O;
5. urea (3 × 19.9 kg N × ha–1) in a solution + Plonvit Z + chelate nickel +
+ MgSO4 × H2O.
The concentration of urea solution used in the different development stages of plants
was: I – 15 %, II – 7.5 % and III – 5 %. Magnesium sulphate was used only in the 1st
Nitrogen Content and Aminoacids Protein Composition of Grain...
525
spring period (3 % solution of magnesium sulphate monohydrate). Plonvit Z was used
in quantities of 1 × dm3 ha–1, and Ni chelate 1 × dm3 ha–1 (5 g Ni × 1 dm–3). The content
of elements [g × kg–1] in Plonvit Z was as follows:
N
Mg
S
Mn
Fe
Zn
Cu
B
Ti
Mo
Na
100
24
20
11
10
10
9
0.7
0.1
0.05
13
Plant protection products Juwel TT 483 SE (epoksykonazol 83 g × dm–3, krezoksym
metylowy 83 g × dm–3, fenpropimorf 317 g × dm–3), Tango Star 334 SE (fenpropimorf
250 g × dm–3, epoksykonazol 84 g × dm–3), Maraton 375 SC (pendimetalina 250 g × dm–3,
izoproturon 125 g × dm–3), Alert 374 SC (flusilazol 125 g × dm–3, karbendazym
250 g × dm–3) were used.
The weather conditions in the years of experiments were different. The rainfalls were
quite diverse, and the air temperature in both years was similar to average from
perennial. In year 2003 during vegetation period draught occurred, but rainfalls which
occurred in September and October greatly increase the humidity of soil as precipitation
was greater than perennial average. In those weather conditions the emergence of winter
wheat was regular. Before entering the winter break period, plants made the spreading
stage well. The spring (except from May) and the first half of the 2004 summer was
characterized by higher precipitation than perennial average. In those conditions the
development of winter wheat was proper. High rainfalls which occurred in July
lengthen the vegetative period of about 2 weeks. In September and partly in October
high rainfalls deficiency has taken place. In those conditions the emergence of winter
wheat was delayed and very irregular. In the third decade of September and in the
October rainfalls which occurred made the emergence more regular and made the
development of plants further. April in year 2005 was characterized by high deficiency
of rainfalls and the second decade of this month was cold with ground froze up to –8 oC
occurred. Higher rainfalls took place in May but with the periodical cold the vegetation
was not getting better as expected. However, June was quite hot with heavy rains which
made the harvest delayed.
The winter wheat was harvested 13.08.2004 and 18.08.2005. In the wheat grain we
determined the total protein content with Kjel-Tec Auto Plus 1030 apparatus, using the
6.25 conversion. Moreover, the composition and content of amino acids was measured
by using an ion exchange chromatography Microtech 339 M apparatus in the Central
Apparatus Laboratory of University of Life Sciences in Lublin. The results were
statistically analysed with variance analysis method with a level of relevance equalling
to 0.05. To compare the statistical significant differences the Tukey test was used.
The differentiation for the total nitrogen content and amino acid protein composition
under the influence of experimental factors proved to be statistically insignificant. Upon
application of EDTA-Ni increased the amount and content of endogenous amino acids
526
as well as leucine and lysine in protein, while reducing the total protein content.
Endogenous amino acids are very important in wheat, not only forms the protein but is
also related to wheat protein quality. Li [12], has shown that gliadin contains proline,
glutamic acid, and cysteine; albumin contains aspartic acid, arginine, and histidine; and
globulin contains alanine, aspartic acid, glycine, and cysteine. Non-essential amino
acids are also related to the gluten, which affect the wheat baking quality [13, 14].
The total protein content in both years of study was highest at sites 1, 2 and 4, where
chelate nickel was not used. The variability of weather conditions in years had
a significant impact for the total protein content in grain, as illustrated by the results of
research across the country (Table 1).
Table 1
The content of total protein in winter wheat grain [g × kg ]
–1
Years
Average results of own study
Average results for country
(winter varieties)*
2004
102.1
116.0
2005
121.0
123.0
* [15, 16].
The course of the weather in 2005 was more conducive for protein storage in wheat
grain than in 2004, because the protein accumulation in grain, which gives it more
desirable baking properties, is higher in small amounts of rainfall and high temperature
during the period from heading until the wax maturity of wheat [17, 18]. In 2004, there
was double the amount of precipitation in June than in 2005, and a lower temperature in
July of up to a few degrees.
Table 2
The share of amino acids protein composition of grain of winter wheat [%]
Experimental objects
Amino acids
1
2
3
4
5
Amino acids percentage in protein
Endogenous
Asparagine
Asp
5.05
4.60
4.55
3.92
4.66
Tyrosine
Tyr
3.32
3.23
3.48
3.23
2.63
Arginine
Arg
4.40
4.57
4.82
4.53
4.60
Serine
Ser
4.53
4.18
4.04
3.72
4.23
Glutamine
Glu
30.06
29.23
30.41
26.68
30.33
Proline
Pro
4.93
5.36
5.38
4.78
5.81
Glycine
Gly
3.70
3.46
3.73
3.64
4.03
Alanine
Ala
3.06
2.91
3.07
2.89
3.31
527
Experimental objects
Amino acids
1
2
3
4
5
Amino acids percentage in protein
Exogeneous
Threonine
Thr
3.47
3.44
3.29
3.00
3.38
Valine
Val
4.21
3.75
4.08
3.90
4.09
Isoleucine
Ile
3.32
3.30
3.31
3.20
3.09
Leucine
Leu
7.93
7.54
7.98
7.21
8.17
Phenylanaline
Phe
6.31
6.28
6.04
5.79
5.94
Histidine
His
2.51
2.87
2.86
2.63
2.47
Lysine
Lys
2.49
2.57
2.75
2.55
2.72
3.35
3.46
3.95
3.28
Sulphur (exogenous)
Cysteine sulfonic acid CySO3H
Methionine sulphone MeSO3
3.18
6.71
3.35
3.45
3.87
3.56
The sum of amino acids
95.94
94.04
96.37
89.41
96.23
Total protein [g × kg–1 d.m.]
107.55
116.5
108.3
112.4
103.95
LSD(0.05) between objects – n.s.
The different fertilization factors had an influence on the amount of amino acids in
wheat protein (Fig. 1). Places where chelate Ni was used, were distinguished with the
largest sum of amino acid; however, the use of Plonvit Z trace element fertilizer (object
4) was characterised with less than over 50 [g × kg–1] of the sum of amino acids in
1000
980
960
963.7
959.4
962.3
72.2
LSD
940.4
[g × kg–1]
940
1. N (soil application)
2. N (foliar application)
3. N + Ni
4. N + Plonvit Z
5. N + Ni + Plonvit Z
LSD0.05
920
894.1
900
880
860
840
371.5
365.6
369.4
361.1
367.0
9.72
LSD
820
800
Average
Fig. 1. The total sums of amino acids in protein of winter wheat (in white squares are exogenous sums)
528
relation to other objects. Among the essential exogenous amino acids, threonine, leucine
and phenylalanine were reduced.
The lysine was limiting amino acid, which is usually the first limiting amino acid for
cereals [19]. The largest of its contents were in chelate nickel addition. This element
also affects the increase in leucine – amino acid involved in the process of muscle
growth.
The largest sum of exogenous amino acid (among objects with foliar feeding) were
characterised with the protein of wheat foliar fertilized with urea including EDTA-Ni(II)
– 3 and 5 objects. The fertilizer trace element Plonvit Z influenced the reduction in the
amount of these amino acids mainly due to reduction of threonine, leucine and
phenylanaline content as well as endogenous amino acids as a result of low asparagine,
serine, glutamine and proline content. The composition of grain protein in the last
experimental object was characterized by highest content of proline, glycine, alanine
and leucine amino acids but lowest izoleucine and histidine. Soil application of urea
comparing with rest of objects had highest asparagine, serine, threonine, valine and
CySO3H but lowest arginine and lysine contents.
Conclusions
1. The fertilizer factors did not have a statistically significant effect on the total
protein content and amino acid composition of winter wheat grain, but some trends did
appear.
2. Both chelate Ni and Plonvit Z influenced the reduction in the amount of the total
protein content in winter wheat grain in comparison with foliar feed with urea.
3. Under the influence of urea foliar application with chelate Ni, a gradual increase
was witnessed in the amount of amino acids, mainly through the endogenous
non-essential amino acids.
4. An addition of the fertilizer trace element Plonvit Z to urea resulted in a decrease
in the amount of amino acids both endo- and exogenous (threonine, leucine and
phenylalanine).
References
[1] Skrabka H.: Zasady regulacji metabolizmu u roœlin. AR, Wroc³aw 1996.
[2] O’Neill P.: Chemia œrodowiska. Wyd. Nauk. PWN, Warszawa–Wroc³aw 1998.
[3] Amaya-Farfan J. and Bertoldo Pacheco M.T.: Amino Acids Properties and Occurrence, [in:] Encyclopedia of Food Sciences and Nutrition, 2003, 181–191.
[4] Gnyœ J.: http://www.modr.mazowsze.pl/new/index.php?option=com_content&view=article&id=753:przegldbiochemiczny-zbo-najczciej-stosowanych-w-ywieniu-zwierzt&catid=111&Itemid=185, 2009.
[5] Petkov K., Bobko K., Biel W. and Jaskowska I.: Folia Univ. Agric. Stetin., Ser. Agricult. 2007,
247(100), 141–144.
[6] Brown P.H., Welch R.M., Cary E.E. and Checkai R.T.: J. Plant Nutr. 1987, 10, 2125–2135.
[7] Mahler R.L.: USDA Forest Service Proc. 2004, RMRS-P-33, 26–29.
[8] Marschner H.: Mineral nutrition of higher plants. Academic Press, New York 1995.
[9] Sirko A. and Brodzik R.: Acta Biochem. Polon. 2000, 47(4), 1189–1195.
[10] Polacco J.C.: Plant Physiol. 1977, 59, 827–830.
[11] Klucas R.V., Hans F.J., Russell S.A. and Evans H.J.: Proc. Natl. Acad. Sci. USA 1983, 80, 2253–2257.
[12]
[13]
[14]
[15]
[16]
[17]
[18]
[19]
529
Li Z.Z.: J. Triticeae Crops 1984, 2, 6–9.
Pena E., Bernardo A., Soler C. and Jouve N.: Euphytica 2005, 143, 169–177.
Wieser H.: Eur. Food Res. Technol. 2000, 211, 262–268.
Rothkaehl J.: Przegl. Zbo¿. M³yn. 2005, (1), 9–13.
Rothkaehl J. and Stêpniewska S.: Przegl. Zbo¿. M³yn. 2006, (1), 2–6.
Goodling M.J. and Smith G.P.: Fifth Congress ESA 1998, 1, 229–230.
Kocoñ A. and Su³ek A.: Ann. UMCS, Sec. E, 2004, 59(1), 471–478.
Pisulewska E., Œcigalska B. and Szymczyk B.: Folia Univ. Agric. Stetin., Ser. Agricult. 2000, 206(82),
219–224.
ZAWARTOŒÆ AZOTU I SK£AD AMINOKWASOWY BIA£KA ZIARNA PSZENICY OZIMEJ
DOKARMIANEJ DOLISTNIE MOCZNIKIEM I NAWOZAMI MIKROELEMENTOWYMI
Katedra Chemii Rolnej i Œrodowiskowej
Uniwersytet Rolniczy w Lublinie
Abstrakt: Doœwiadczenie polowe przeprowadzono w latach 2003–2005 na glebie p³owej (Haplic Luvisols),
kompleks pszenny wadliwy metod¹ bloków losowych w 4 powtórzeniach. Gleba mia³a kwaœny odczyn (pHKCl
– 5,3) i naturaln¹ zawartoœæ pierwiastków œladowych. Roœlin¹ testow¹ by³a pszenica ozima odmiana
jakoœciowa (klasa A) – Rywalka. Celem badañ by³o okreœlenie wp³ywu dokarmiania dolistnego mocznikiem
oraz chelatem niklu EDTA-Ni(II) i Plonvitem Z na zawartoœæ azotu ogó³em i sk³ad aminokwasowy ziarna
pszenicy ozimej. Zró¿nicowanie zawartoœci azotu ogó³em i sk³adu aminokwasowego bia³ka pod wp³ywem
czynników doœwiadczalnych okaza³o siê statystycznie nieistotne. Pod wp³ywem EDTA-Ni zwiêkszeniu
ulega³a suma aminokwasów endogennych oraz zawartoœæ leucyny i lizyny w bia³ku, zaœ zmniejszeniu
zawartoœæ bia³ka ogólnego.
S³owa kluczowe: azot, aminokwasy, pszenica ozima, dolistne dokarmianie, mocznik, mikroelementy
A
Vol. 18, No. 4
2011
Stefan GRZEGORCZYK1, Kazimierz GRABOWSKI1
and Jacek ALBERSKI1
NITROGEN ACCUMULATION BY SELECTED SPECIES
OF GRASSLAND LEGUMES AND HERBS
GROMADZENIE AZOTU PRZEZ WYBRANE GATUNKI
ROŒLIN MOTYLKOWATYCH I ZIÓ£ £¥KOWYCH
Abstract: The study was conducted in 1998–2000 (June – first ten days of July) in the Olsztyn Lakeland.
A total of 444 plant samples were analyzed, including 123 collected in organic soils. The analysis covered
Trifolium pratense, Trifolium repens, Lotus corniculatus, Lathyrus pratensis, Lotus uliginosus, Vicia cracca,
Taraxacum officinale, Achillea millefolium, Plantago lanceolata, Alchemilla vulgaris, Heracleum sibiricum
and Cirsium oleraceum.
The average total nitrogen content of mineral and organic soils ranged from 1.35 to 3.40 g × kg–1 and from
9.78 to 14.1 g × kg–1, respectively. Significant differences were found in the nitrogen content of biomass of the
analyzed plant species. The average nitrogen content of plants varied from 17.0 to 34.4 g × kg–1 d.m.. The
highest nitrogen accumulation levels were observed in Vicia cracca grown in organic soils, and the lowest in
Alchemilla vulgaris grown in mineral soils. The coefficient of variation in the above parameter did not exceed
20 %, thus suggesting that the noted values may be considered typical of the studied species.
Keywords: grasslands, legumes, herbs, nitrogen, soil.
The quality of animal feedstuffs is largely dependent on the species composition of
grasslands. Legumes are a valuable component of grassland swards. According to
Novoselova and Frame [1], legumes have a beneficial influence on grassland productivity as they contribute to a high yield of total and digestible protein, a reduction in
nitrogen mineral fertilization, an increase in the nitrogen content of soil, a decrease in
groundwater nitrate contamination and an improvement in the quality of feedstuffs and
animal products.
The most important legume species grown in grasslands in northern Europe are
Trifolium repens, Trifolium pratense, Trifolium hybridum, Medicago sativa and Lotus
corniculatus. In Western Europe, the most common species is Trifolium repens,
accompanied by Lotus corniculatus and Lotus uliginosus which – in contrast to other
legumes – can be grown under extreme conditions [1, 2].
1
Department of Grassland Management, University of Warmia and Mazury in Olsztyn, pl. £ódzki 1,
10–727 Olsztyn, Poland, phone: +48 89 523 34 93, fax: +48 89 523 43 81, email: [email protected]
532
Stefan Grzegorczyk et al
Herbs are also valuable components of grassland communities. They are a rich
source of essential nutrients with therapeutic and medicinal properties as well as other
compounds that affect feed up take and utilization by animals [3]. In comparison with
grasses, herbaceous plants contain larger amounts of nutrients, particularly mineral
compounds and total protein. Although the share of herbs in grassland sward should not
exceed 10 %, their economic importance remains high. The most common herb species
are, among others, Taraxacum officinale, Achillea millefolium, Plantago lanceolata and
Alchemilla vulgaris. In view of the above, the objective of this study was to determine
the levels of nitrogen accumulation by common species of grassland legumes and herbs.
The study was conducted in 1998–2000 (June – first ten days of July) in the Olsztyn
Lakeland, in permanent grassland communities with at least 5 % share of the following
legume and herb species: Trifolium pratense, Trifolium repens, Lotus corniculatus,
Lathyrus pratensis, Lotus uliginosus, Vicia cracca, Taraxacum officinale, Achillea
millefolium, Plantago lanceolata, Alchemilla vulgaris, Heracleum sibiricum and Cirsium
oleraceum. A total of 444 plant samples were analyzed, including 123 collected in
organic soils (Table 1). The total nitrogen content of soil and plants was determined by
the Kjeldahl method [4].
Table 1
Number of plant samples
Species
Lathyrus pratensis
Lotus corniculatus
Lotus uliginosus
Trifolium pratense
Trifolium repens
Vicia cracca
Achillea millefolium
Alchemilla vulgaris
Cirsium oleraceum
Heracleum sibiricum
Plantago lanceolata
Taraxacum officinale
Total
Site
Mineral soil
Organic soil
29
23
22
25
26
20
33
31
18
29
32
33
321
13
—
29
—
—
14
19
17
31
—
—
—
123
The nitrogen content of plants grown in mineral soils varied over a wide range of
12.0 to 39.4 g × kg–1 (Table 2). Legumes accumulated larger quantities of nitrogen. The
highest average nitrogen content was noted in Lotus corniculatus, Lathyrus pratensis,
Nitrogen accumulation by selected species of grassland legumes and herbs
533
Lotus uliginosus and Trifolium pratense, while the lowest in Plantago lanceolata,
Achillea millefolium, Alchemilla vulgaris and Taraxacum officinale. The coefficient of
variation in the above parameter was relatively low (from 10.4 % to 17.8 %), thus
suggesting that the noted values may be considered typical of the studied species. The
average nitrogen content of mineral soils ranged from 1.35 to 3.40 g × kg–1 (Table 3).
Cirsium oleraceum and Lotus uliginosus were found in nitrogen-abundant soils,
whereas Trifolium repens and Taraxacum officinale were reported from nitrogen-poor
soils.
Table 2
Average nitrogen content of plants grown in mineral soils
N content [g × kg–1 d.m.]
Minimum
Maximum
Average
Coefficient of variation
[%]
22.4
18.7
25.6
19.4
22.4
21.6
19.5
17.4
12.0
14.7
13.1
13.4
39.4
38.2
39.0
38.1
32.2
33.3
30.7
27.4
25.1
23.8
23.2
25.0
31.8
30.6
30.1
29.0
28.3
28.3
24.5
22.1
18.6
18.1
17.9
17.0
16.7
16.3
13.3
15.2
13.6
10.4
11.5
11.7
15.1
11.0
12.8
17.8
Species
Lotus corniculatus
Lathyrus pratensis
Lotus uliginosus
Trifolium pretense
Trifolium repens
Vicia cracca
Heracleum sibiricum
Cirsium oleraceum
Alchemilla vulgaris
Plantago lanceolata
Table 3
Average nitrogen content of mineral soils
N content [g × kg–1]
Minimum
Maximum
Average
[%]
1.70
0.91
1.00
0.95
0.50
0.70
0.88
0.50
0.46
0.67
0.50
0.46
7.70
7.70
4.90
4.92
3.90
7.70
3.96
7.70
3.70
3.70
3.70
3.30
3.40
2.95
2.50
2.33
2.00
1.90
1.87
1.60
1.50
1.49
1.40
1.35
44.3
57.3
46.6
44.2
43.1
73.6
52.0
80.4
52.6
54.0
54.2
54.6
Species
Cirsium oleraceum
Lotus uliginosus
Alchemilla vulgaris
Lathyrus pratensis
Heracleum sibiricum
Vicia cracca
Plantago lanceolata
Lotus corniculatus
Trifolium pratense
Trifolium repens
534
The nitrogen content of plants grown in organic soils also varied widely, from 13.3 to
47.4 g × kg–1 (Table 4). Again, legumes were characterized by substantially higher
nitrogen concentrations. The highest nitrogen content was determined in Vicia cracca,
and the lowest in Alchemilla vulgaris. Similarly as in plants grown in mineral soils, the
coefficient of variation in the above parameter was relatively low (from 11.7 % to
18.2 %), therefore the noted values may be considered characteristic of the analyzed
species. The average nitrogen content of organic soils ranged from 9.8 to 14.1 g × kg–1
(Table 5). Achillea millefolium was reported from soils most abundant in nitrogen,
while Lathyrus pratensis preferred soils least abundant in this nutrient.
Table 4
Average nitrogen content of plants grown in organic soils
Minimum
Maximum
Average
[%]
31.2
24.0
20.2
15.5
16.2
13.3
47.4
37.1
33.0
31.0
28.5
27.7
34.4
30.7
30.1
23.5
22.4
18.6
12.1
11.7
12.3
18.2
14.5
18.0
Species
Vicia cracca
Lotus uliginosus
Lathyrus pratensis
Cirsium oleraceum
Alchemilla vulgaris
Table 5
Average nitrogen content of organic soils
Minimum
Maximum
Average
[%]
5.60
3.84
3.80
2.65
2.70
4.66
27.8
27.8
27.8
25.9
27.8
20.0
14.1
12.9
12.2
11.3
10.0
9.8
47.9
61.0
59.2
61.6
59.7
49.6
Species
Lotus uliginosus
Cirsium oleraceum
Vicia cracca
Alchemilla vulgaris
Lathyrus pratensis
Based on a statistical analysis of the obtained results, the studied plant species were
divided into four groups differing with respect to total nitrogen content (Table 6). Vicia
cracca grown in organic soils, characterized by the highest nitrogen content, constituted
the first group. The second group comprised the other legume species, Lotus
corniculatus, Lotus uliginosus, Lathyrus pratensis, Trifolium repens and Trifolium
pratense. The third groups was formed by Heracleum sibiricum, Cirsium oleraceum and
Achillea millefolium grown in organic soils. The fourth group included plants with the
lowest total nitrogen content: Alchemilla vulgaris as well as Plantago lanceolata,
Achillea millefolium and Taraxacum officinale grown in mineral soils.
Nitrogen accumulation by selected species of grassland legumes and herbs
535
Table 6
Significance of differences in the nitrogen content of plants
Species
Vicia cracca
Soil
N [g × kg–1]
Homogeneous groups

*O*
34.4
Lotus corniculatus
M
31.8
Lotus uliginosus
O
30.7

Lathyrus pratensis
M
30.6

Lotus uliginosus
M
30.1

Lathyrus pratensis
O
30.1

Trifolium pratense
M
29.0
Trifolium repens
M
28.3

Vicia cracca
M
28.3

Heracleum sibiricum
M
24.5

Cirsium oleraceum
O
23.5

O
22.4

Cirsium oleraceum
M
22.1
Alchemilla vulgaris
O
18.6

M
18.1

Alchemilla vulgaris
M
17.9

M
17.7

Plantago lanceolata
M
17.0

* O – organic soil, M – mineral soil.
In a study by Kacorzyk and Szewczyk [5], legumes contained the largest quantities
of nitrogen, whereas protein content was 16–20 % higher in herbs than in grasses.
Tsialtas et al [6] demonstrated that Taraxacum officinale accumulated more nitrogen
than grasses. Differences in the nitrogen content of legumes and other grassland species
were also reported by Bandeff et al [7], Eisenhauer and Scheu [8]. Goh and Bruce [9],
Grzegorczyk and Alberski [10], and Gylfadottir [11].
Conclusions
1. Among the analyzed plant species, legumes – in particular Vicia cracca grown in
organic soils – accumulated significantly more nitrogen. Plantago lanceolata, Achillea
millefolium, Alchemilla vulgaris and Taraxacum officinale grown in mineral soils had
the lowest nitrogen content.
2. The tested plant species were collected from soils with a different total nitrogen
content (in most cases, the coefficient of variation did not exceed 50 %).
3. Despite considerable differences in the nitrogen content of plants, in the majority
of cases the recorded average nitrogen concentrations may be considered typical of the
studied species, as confirmed by low coefficients of variation.
536
References
[1] Novoselova A. and Frame J.: Proc. of the 14th General Meeting of the European Grassland Federation,
Lahti, Finland, 1992, 87–96.
[2] Grzegorczyk S., Bernatowicz T., Grabowski K. and Alberski J.: Zesz. Probl. Post. Nauk Roln., 2001,
479, 95–100.
[3] Kostuch R.: Zesz. Probl. Post. Nauk Roln., 1996, 442, 277–284.
[4] PN-EN ISO 5983-2: 2006.
[5] Kacorzyk P. and Szewczyk W.: £¹karstwo w Polsce, 2008, 11, 77–85.
[6] Tsialtas J.T., Kassioumi M.T. and Veresogloud D.S.: Biol. Plant., 2005, 49(1): 133–136.
[7] Bandeff1 J.M., Pregitzer K.S., Loya1 W.M., Holmes W.E. and Zak D.R.: Plant and Soil, 2006, 282,
251–259.
[8] Eisenhauer N. and Scheu S.: Soil Biol. & Biochem., 2008, 40, 2650–2659.
[9] Goh K.M. and Bruce G.E.: Agricult., Ecosyst. and Environ., 2005, 110, 230–240.
[10] Grzegorczyk S. and Alberski J.: Grassland Scie. in Europe, 2004, 9, 921–923.
[11] Gylfadóttir T., Helgadóttir Á. and Høgh-Jensen H.: Plant Soil, 2007, 297, 93–104.
GROMADZENIE AZOTU PRZEZ WYBRANE GATUNKI ROŒLIN MOTYLKOWATYCH
I ZIÓ£ £¥KOWYCH
Katedra £¹karstwa
Uniwersytet Warmiñsko-Mazurski w Olsztynie
Abstrakt: Badania prowadzono w latach 1998–2000 (czerwiec – pierwsza dekada lipca) na terenie Pojezierza
Olsztyñskiego. £¹cznie przebadano 444 próbek roœlinnych, w tym 123 pochodz¹ce z gleb organicznych.
Badaniami objêto Trifolium pratense, Trifolium repens, Lotus corniculatus, Lathyrus pratensis, Lotus
uliginosus, Vicia cracca, Taraxacum officinale, Achillea millefolium, Plantago lanceolata, Alchemilla
vulgaris, Heracleum sibiricum i Cirsium oleraceum.
Œrednia zawartoœæ azotu ogólnego w glebie mineralnej waha³a siê w granicach 1,35–3,40 g × kg–1,
a w glebie organicznej 9,78–14,1 g × kg–1. Stwierdzono statystycznie istotne ró¿nice w zawartoœci azotu
w biomasie poszczególnych gatunków. Œrednia zawartoœæ azotu w roœlinach waha³a siê od 17,0 do
34,4 g × kg–1 sm. Najwiêcej azotu gromadzi³a Vicia cracca wystêpuj¹ca na glebach organicznych, najmniej zaœ
Alchemilla vulgaris wystêpuj¹cy na glebach mineralnych. Mo¿na to uznaæ za charakterystyczn¹ w³aœciwoœæ
tych gatunków, bowiem wspó³czynnik zmiennoœci tej cechy u poszczególnych gatunków nie przekracza³
20 %.
S³owa kluczowe: u¿ytki zielone, motylkowate, zio³a, azot, gleba
A
2011
Vol. 18, No. 4
Gra¿yna HARASIMOWICZ-HERMANN1 and Janusz HERMANN2
NITROGEN BIOCONVERSION
AND FODDER PROTEIN RECOVERY
FROM DISTILLERY SPENT WASH
BIOKONWERSJA AZOTU I ODZYSK BIA£KA PASZOWEGO
Z WYWARU GORZELNICZEGO
Abstract: Distillery spent wash is formed as a by-product in spirit production, and its considerable amount
has been used as animal feed so far. Currently, however, both stock decrease and changing animal feeding
technology caused a significant reduction in use of spent wash for animal food. Pursuant to the law in force,
distillery spent wash can be intended for recovery in order to improve soil physical, chemical or biological
properties and to provide plants with nutrients or enhance soil fertility. It should be applied in such a way and
in such amounts so that its introduction into soil cannot cause exceeding permissible values of heavy metals
(Cr, Pb, Cd, Hg, Ni, Zn, Cu), even after long-term application. When heavy metal content in spent wash is
low, it can be used in so large amounts that excessive nitrogen becomes a problem, since its amount is not
limited in legal acts. The most beneficial method for lowering nitrogen content in distillery spent wash is to
incorporate it into yeast biomass.
The aim of this study was to estimate a possibility and extent of nitrogen reduction in distillery spent wash
subjected to refermentation by means of fodder yeast, utilizing components which were not used in alcoholic
fermentation. The mean content of total nitrogen in raw distillery spent wash amounted to 44.3 g × kg–1 d.m.
After yeasting of raw distillery spent wash with and without an addition of phosphorus in two doses, ie
8.1 g × kg–1 and 16.2 g × kg–1, the reduction of total nitrogen content obtained in the filtrate ranged from 66 %
to 86.2 %. Biomass obtained after filtration and drying was processed for foods for animals, and the filtrate
containing from 6.10 to 15.1 g × kg–1 d.m. nitrogen was intended for use in agriculture.
The manurial value of distillery spent wash is known and appreciated, but the current problem in its
management is the fact that large amounts of spent wash with considerable nitrogen content are generated in
continuous production and it can be applied only beyond plant growing season.
Refermentation of spent wash tested in the present study facilitates mass condensation and filtrate
purification, but above all, it reduces the content of nitrogen in it. This will enable the rational utilization of
filtrate, without risk of introducing the excess of nitrogen into soil and, consequently, ground water pollution.
Keywords: distillery spent wash, nitrogen bioconversion, nitrogen content reduction
1
Department of Plant Cultivation, Faculty of Agriculture and Biotechnology, University of Technology
and Life Sciences in Bydgoszcz, ul. Ks. Kordeckiego 20, 85–225 Bydgoszcz, Poland, phone/fax: +48 52 342
79 74, email: [email protected]
2
Department of Environmental Chemistry, Faculty of Agriculture and Biotechnology, University of
Technology and Life Sciences in Bydgoszcz, ul. Bernardyñska 6, 85–029 Bydgoszcz, Poland, phone/fax:
+48 52 374 95 02, email: [email protected]
538
Gra¿yna Harasimowicz-Hermann and Janusz Hermann
Distillery spent wash is a by-product formed in spirit production and due to elements
it contains it should be managed rationally. So far, its considerable amount has been
used as animal food. However, because of stock decrease and changes in animal feeding
technology, the use of spent wash for animal feed decreased significantly. The manurial
value of distillery spent washes is known and appreciated [1–3]. When the content of
heavy metals in distillery spent wash is low, its considerable amounts can be intended
for agricultural use and then the excess of nitrogen becomes the limiting factor. The
regulation of the Ministry of Environment of 14 November 2007 on the process of R10
recovery [4] presents conditions of agricultural utilization of spent wash. It must be
applied beyond the plant growing season and evenly distributed throughout soil area,
but only to a depth of 30 cm. Spent wash is covered or mixed with soil, except when
used on grasslands and long-term plantations. A field on which spent wash is applied
should have a ground water-table level deeper than 1.5 m. It can be used on soils on
which the admissible values of concentration of substances defined in the regulation of
the Ministry of Environment of 9 September 2002 on soil and earth quality standards
are not exceeded [5]. The rule binding assumes that its introduction into soil will not
result in exceeding admissible amounts of heavy metals (Cr, Pb, Cd, Hg, Ni, Zn, Cu –
determined in the above regulation), even after long-term application.
Considerable amounts of spent wash can be managed in this way; however, at the
same time, higher amounts of nitrogen are introduced into soil than it is necessary for
rational plant fertilization. In legal acts, a dose of spent wash applied into soil is not
limited in respect of the amount of nitrogen introduced along with it.
The aim of this study was to estimate the possibility and extent of nitrogen content
reduction in distillery spent wash by means of subjecting it to refermentation using
fodder yeast [6], utilizing components, including nitrogen, which were not used in
alcoholic fermentation. As a result of this process, we obtain a condensed suspension of
yeast biomass, which is separated from yeasted spent wash and intended for fodder and
filtrate, which is transmitted to a system of distribution to the fields or redirected to the
technological process. Nitrogen bioconversion and fodder protein recovery from
distillery spent wash intended for use in agriculture enables the rational nitrogen
utilization.
The research material was raw distillery spent wash, whose chemical composition
(mean of three-day production) was listed in Table 1. Investigations of spent wash
characteristics in respect of its usefulness for application in agriculture were made in an
accredited laboratory, determining: pH value with the electrometric method in water;
dry matter (d.m.) content, organic substance content, and the contents of total nitrogen,
total phosphorus, calcium and magnesium, EPA with the 7000AM method; heavy metal
content: lead, cadmium, chromium, copper, nickel and zinc, in a representative sample
of spent wash – EPA with the 7000A method and mercury content with the Lumen
method 03AE07081:2001.
The present study was carried out on three batches of distillery spent wash from
successive daily productions, treating them as replications. Each test in the experiment
Nitrogen Bioconversion and Fodder Protein Recovery from Distillery Spent Wash
539
was made on 100 kg of spent wash. Distillery spent wash: 1) raw; 2) with an addition of
8.1 g × kg–1 phosphorus; 3) with an addition of 16.2 g × kg–1 phosphorus; was subjected
to yeasting. After three days, the yeast sludge was separated and nitrogen content was
once more determined in the filtrate obtained. The significance of differences in the
nitrogen content reduction level in the filtrate from yeasted spent wash was assessed
using Tukey’s test.
Table 1
Chemical composition of raw distillery spent wash
Specification
Unit
Results
pH value in H2O
Dry matter content in fresh mass of spent wash
Organic matter content
Total nitrogen content (N)
Total phosphorus content (P)
Calcium content (Ca)
Magnesium content (Mg)
Cadmium content (Cd)
Lead content (Pb)
Mercury content (Hg)
Zinc content (Zn)
Copper content (Cu)
Chromium content (Cr)
Nickel content (Ni)
pH
%
g × kg–1 d.m.
g × kg–1 d.m.
g × kg–1 d.m.
g × kg–1 d.m.
g × kg–1 d.m.
mg × kg–1 d.m.
mg × kg–1 d.m.
mg × kg–1 d.m.
mg × kg–1 d.m.
mg × kg–1 d.m.
mg × kg–1 d.m.
mg × kg–1 d.m.
12.8
4.43
719.0
44.3
8.1
24.0
1.7
1.19
12.4
0.096
129
5.07
5.50
8.79
The biomass obtained after filtration and drying was processed into feeds for
animals, and the filtrate was intended for use in agriculture.
A technical and economic conception of conditioning – yeasting of spent wash
and leachate purification came into being in the Research and Development Station
‘FOSSBAC’ in Wiag near Swiecie. Its technological details are under patent protection.
In a daily production of alcohol in a distillery processing 30 Mg cereal, 300 Mg spent
wash is obtained with a mean content of 4.43 % dry matter, ie 13.3 Mg d.m. and 286.7 Mg
liquid fraction with a load of oxidizable organic matter determined as 40–50 g × dm–3 O2.
Table 2 presents the amount of organic matter, nutrients and heavy metals introduced
into soil with diversified doses of distillery spent wash. The amount of heavy metals,
whose limits according to the Regulation of the Minister of the Environment of
1 August 2002 on municipal sewage sludge § 3.3 [7] are given in Table 2, column 3, is
the factor limiting the size of spent wash dose applied in agriculture. From the chemical
composition determined, it appears that cadmium content – 1.19 mg × kg–1 d.m. – limited
(more than the other heavy metals) the dose of distillery spent wash to 16.8 Mg × ha–1
d.m. spent wash. A higher dose could cause exceeding of permissible amounts of this
heavy metal – 20 g × ha–1 × year–1 Cd.
kg
kg
kg
kg
g
g
g
g
g
g
g
Amount of total phosphorus (P)
Amount of calcium (Ca)
Amount of magnesium (Mg)
Amount of cadmium (Cd)
Amount of plumbum (Pb)
Amount of mercury (Hg)
Amount of zinc (Zn)
Amount of copper (Cu)
Amount of chromium (Cr)
Amount of nickel (Ni)
200
1000
1600
5000
10
1000
20
n.l.**
n.l.**
n.l.**
n.l.**
n.l.**
Limited according
to ME regulation*
introduced into soil on average
during 10 years × ha–1× year–1
87.9
55.0
50.7
1290
0.96
124
11.9
17
240
81
443
7.19
Introduced
in 10 Mg × ha–1 d.m.
spent wash
117
73.2
67.4
1716
1.28
165
15.8
22.6
319
108
589
9.56
Introduced
in 13.3 Mg × ha–1 d.m.
spent wash
(amount obtained from
daily production of alcohol)
148
92.4
85.2
2167
1.61
208
20
28.6
403
136
744
12.1
Introduced in admissible dose
16.8 Mg × ha–1 d.m.
spent wash
* § 3.3 Ministry of Environment Regulation of 1 August 2002 on municipal sewage sludge [7]; ** n.l. – component in the amount which is not limited by the above
regulation.
Mg
Amount of total nitrogen (N)
Units
Amount of organic matter
Specification
Amount of components
Amount of organic matter, nutrients and heavy metals introduced into soil with different doses of raw distillery spent wash
Table 2
540
541
When dry matter content in the analyzed spent wash is equal to 4.43 %, a dose of
fresh matter of the spent wash will be 379.2 Mg × ha–1 year–1 (approximately 380 m3).
12.1 Mg × ha–1 organic matter, 744 kg × ha–1 nitrogen (N), 136 kg × ha–1 phosphorus
(P), 403 kg × ha–1 calcium (Ca) and 28.6 kg × ha–1 magnesium (Mg) will be introduced
with 380 m3 of spent wash.
After separating the yeast fraction from the yeasted distillery spent wash, a significant
reduction of nitrogen content was obtained in the filtrate, irrespective of the additives
applied (Table 3). Nitrogen content reduction in the filtrate in relation to raw spent wash
ranged from 65.9 % to 86.2 %. Phosphorus addition at an amount of 16.2 g × kg–1 to the
yeasted spent wash significantly decreased the content of nitrogen as compared with
that obtained in the filtrate from the yeasted raw spent wash without additives.
Table 3
Changes in nitrogen content in filtrate from yeasted spent wash
Raw material
Raw distillery spent wash
Filtrate from yeasted raw spent wash
(without additives)
with an addition of 8.1 g × kg–1 phosphorus
with an addition of 16.2 g × kg–1 phosphorus
LSD0.05 – for nitrogen content
Total nitrogen content (N)
[ g × kg–1 d.m.]
Nitrogen reduction level (N)
[%]
44.3
—
15.1
65.9
11.1
74.9
6.10
5.009
86.2
Refermentation of spent wash facilitated the mass condensation and the reduction of
nitrogen content in the filtrate. This enables the full utilization of filtrate, without a risk
of introducing the excess of nitrogen into soil and, consequently, ground water
pollution. If nitrogen in spent wash is subjected to bioconversion in the process of
fodder yeast production, from 81 to 201 kg nitrogen is obtained in filtrate from daily
production, depending on the means of yeasting technology (Table 4).
Mean content of total nitrogen in raw distillery spent wash was 44.3 g × kg–1 d.m.
Data presented in Table 2 indicate that the amount of nitrogen in spent wash daily
production amounts to 589 kg. Assuming that the continuous production of the distillery
is 200 days in year, the amount of distillery spent wash amounts to 60 × 103 Mg
including 117.8 Mg of total nitrogen (Table 5).
According to the rules of good agricultural practice, an annual nitrogen dose in plant
cultivation should not exceed on average 170 kg × ha–1. Thus, the field area intended for
the agricultural management of such amount of raw spent wash should amount to 693
ha (Table 6). The filtrate remaining after yearly yeast production contains from 16.2 to
40.2 Mg of nitrogen for management (Table 5). The field area for the agricultural use of
the nitrogen amount contained in the filtrate is considerably lower in relation to the area
needed for raw spent wash and ranges from 95 ha to 236 ha (Table 6).
542
Table 4
Amount of nitrogen introduced into soil with different doses of filtrate
from yeasted spent wash type of filtrate
Amount of total nitrogen (N)
Raw material
Unit
Introduced in
10 Mg × ha–1
d.m. spent wash
Introduced in
13.3 Mg × ha–1 d.m. spent wash
(amount obtained from daily
production of alcohol)
Introduced in
admissible dose
16.8 Mg × ha–1
d.m. spent wash
151
201
254
111
148
186
61
81
102
Filtrate from yeasted raw spent
wash (without additives)
wash with an addition of
8.1 g × kg–1 phosphorus
kg
wash with an addition of
16.2 g × kg–1 phosphorus
Table 5
Nitrogen mass remaining in spent wash or in filtrate during 200 production days of the distillery
Specification
Units
Amount of total nitrogen
(N)
117 800
Filtrate from yeasted raw spent wash (without additives)
40 200
Filtrate from yeasted raw spent wash with an addition of 8.1 g × kg–1
phosphorus
Filtrate from yeasted raw spent wash with an addition of 16.2 g × kg
phosphorus
kg
29 600
–1
16 200
Table 6
Field area for agricultural management of raw distillery spent wash and filtrate
from yeasted spent wash – considering rational utilization
of nitrogen generated during 200 production days of the distillery
Raw material
Units
Field area
693
Filtrate from yeasted raw spent wash (without additives)
236
Filtrate from yeasted raw spent wash with an addition of 8.1 g × kg–1 phosphorus
Filtrate from yeasted raw spent wash with an addition of 16.2 g × kg–1 phosphorus
ha
174
95
The means of spent wash utilization used before involved numerous inconveniences.
In terms of the application of spent wash in agriculture for production of plants intended
for human consumption and fodder – using process R10, as well as its application as
fodder – using process R14, the producers have already received legislative support in
543
the form of legal acts in force [8] and bills which are supposed to come into effect soon.
Dienszczykow [1], Kumider [6] and Labetowicz et al [2] applied spent wash for
fertilization and obtained the direct and consequent growth of plant yield. In a study by
these authors, the dose height was determined by nitrogen content in spent wash
according to plant requirement and an increase in nitrogen content in soil occurred in
spite of balancing the dose. Therefore, large amounts of spent wash applied yearly in
the same fields will pose a threat to the environment. A great deal of inconveniences of
spent wash application can be minimized by means of nitrogen content reduction in
post-production waste.
Conclusions
1. Excessive amount of nitrogen is a factor limiting the application of high doses of
crude spent wash in agriculture (process R10), at the low content of heavy metals.
2. Yeasting of distillery spent wash causes 66 % reduction of nitrogen content in the
filtrate remaining after separating fodder yeast, and the addition of phosphorus
significantly increases the extent of reduction.
3. Bioconversion of nitrogen and recovery of fodder protein from distillery spent
wash intended for use in agriculture enables the rational utilization of nitrogen and
grounds belonging to the distillery.
References
[1] Dienszczykow M.T.: Odpady przemys³u spo¿ywczego i ich wykorzystanie. WNT, Warszawa 1969.
[2] £abêtowicz J., Stêpieñ W., Gutowska A. and Korc M.: Zesz. Probl. Post. Nauk Roln. 2003, 494,
247–254.
[3] Mercik S. and Stêpieñ W.: Rocz. Glebozn. 1992, XLIII(1/2), 61–70.
[4] Rozporz¹dzenie Ministra Œrodowiska z dnia 14 1istopada 2007 r. w sprawie procesu odzysku R10. DzU
Nr 228, poz. 1685.
[5] Rozporz¹dzenie Ministra Œrodowiska z dnia 9 wrzeœnia 2002 r. w sprawie standardów jakoœci gleby oraz
standardów jakoœci ziemi. DzU Nr 165, poz. 1359.
[6] Kumider J.: Utylizacja odpadów przemys³u rolno-spo¿ywczego. Aspekty towaroznawcze i ekologiczne.
Wyd. AE, Poznañ 1996.
[7] Rozporz¹dzenie Ministra Œrodowiska z dnia 1 sierpnia 2002 r. w sprawie komunalnych osadów
œciekowych. DzU Nr 134, poz. 1140.
[8] Rozporz¹dzenia Ministra Œrodowiska z dnia 21 kwietnia 2006 r. w sprawie listy rodzajów odpadów,
które posiadacz odpadów mo¿e przekazaæ osobom fizycznym lub jednostkom organizacyjnym niebêd¹cym przedsiêbiorcami, oraz dopuszczalnych metod ich odzysku. DzU Nr 75, poz. 527.
BIOKONWERSJA AZOTU I ODZYSK BIA£KA PASZOWEGO
Z WYWARU GORZELNICZEGO
1
Katedra Szczegó³owej Uprawy Roœlin, 2 Katedra Chemii Œrodowiska
Uniwersytet Technologiczno-Przyrodniczy w Bydgoszczy
Abstrakt: W produkcji spirytusu wywar gorzelniczy powstaje jako produkt uboczny, a znaczna jego iloœæ
by³a dotychczas zu¿ywana jako pasza dla zwierz¹t. Jednak obecnie zarówno spadek pog³owia, jak i zmiana
technologii ¿ywienia zwierz¹t spowodowa³y, ¿e wykorzystanie wywaru do celów paszowych istotnie siê
544
zmniejszy³o. Zgodnie z obowi¹zuj¹cym prawem, wywar gorzelniczy mo¿e byæ przeznaczony do odzysku,
tak¿e w celu poprawy fizycznych, chemicznych lub biologicznych w³aœciwoœci gleb oraz w celu dostarczenia
roœlinom sk³adników pokarmowych lub zwiêkszenia ¿yznoœci gleb. Powinien byæ stosowany w taki sposób
i w takiej iloœci, aby jego wprowadzenie do gleby nie spowodowa³o przekroczenia w niej dopuszczalnych
wartoœci metali ciê¿kich (Cr, Pb, Cd, Hg, Ni, Zn, Cu), nawet przy d³ugotrwa³ym stosowaniu. Przy niskiej
zawartoœci metali ciê¿kich w wywarze mo¿na go zastosowaæ w tak du¿ych iloœciach, ¿e problemem staje siê
nadmiar azotu, bowiem jego iloœæ nie jest limitowana w aktach prawnych. Najkorzystniejszym sposobem na
obni¿enie zawartoœci azotu w wywarze gorzelniczym jest wbudowanie go w masê dro¿d¿y.
Celem pracy by³o okreœlenie mo¿liwoœci i stopnia ograniczenia zawartoœci azotu w wywarze gorzelniczym
poddanym ponownej fermentacji, przy u¿yciu dro¿d¿y paszowych, wykorzystuj¹c sk³adniki nie zu¿yte
w fermentacji alkoholowej. Œrednia zawartoœæ azotu ogó³em w surowym wywarze gorzelniczym wynosi³a
44,3 g × kg–1 s.m. Po zadro¿d¿owaniu surowego wywaru gorzelniczego, bez oraz z dodatkiem fosforu
w dwóch dawkach 8,1 g × kg–1 i 16,2 g × kg–1, osi¹gniêto redukcjê zawartoœci azotu ogó³em w filtracie od
65,9 % do 86,2 %. Otrzymana po filtracji i wysuszeniu biomasa zosta³a przetworzona na œrodki ¿ywieniowe
dla zwierz¹t, a filtrat zawieraj¹cy od 6,10 do 15,1 g × kg–1 s.m. azotu, przeznaczony do stosowania
w rolnictwie.
Wartoœæ nawozowa wywaru gorzelniczego jest znana i doceniana, ale aktualnie problemem w zagospodarowaniu jest to, ¿e w produkcji ci¹g³ej powstaj¹ du¿e iloœci wywaru o znacznej zawartoœci azotu i mo¿na
go stosowaæ jedynie poza sezonem wegetacji roœlin.
Testowana w badaniach w³asnych ponowna fermentacja wywaru u³atwia³a zagêszczanie masy i oczyszczenie filtratu, ale przede wszystkim ogranicza³a zawartoœæ w nim azotu. Pozwoli to na racjonalne
wykorzystanie filtratu, bez obawy wprowadzenia nadmiaru azotu do gleby i w konsekwencji zanieczyszczenia
wód podziemnych.
S³owa kluczowe: wywar gorzelniczy, biokonwersja azotu, obni¿enie zawartoœci azotu
A
Vol. 18, No. 4
2011
Czes³awa JASIEWICZ and Agnieszka BARAN1
COMPARISON OF THE EFFECT OF MINERAL
AND ORGANIC FERTILIZATION ON THE COMPOSITION
OF AMINO ACIDS IN GREEN BIOMASS MAIZE
PORÓWNANIE WP£YWU MINERALNEGO
I ORGANICZNEGO NAWO¯ENIA NA SK£AD AMINOKWASÓW
W ZIELONEJ MASIE KUKURYDZY
Abstract: The research aimed at an assessment of the effect of mineral and organic fertilization on the
composition of amino acids in maize San c.v. The investigations were conducted as a pot experiment. The
experimental design comprised 11 treatments differing with the dose and kind of supplied fertilizers. Mineral
salts (NPK), farmyard manure, compost, municipal and industrial sewage sludges were used as the source of
nutrients for maize. Two levels of NPK fertilization were considered in the experiment. Doses of farmyard
manure, compost, municipal and industrial sludge were established on the basis of nitrogen fertilization level.
Determined were 17 amino acids: theronine, leucine, phenylalanine, histidine, lysine, methionine, arginine,
valine, isoleucine, tyrosine, cysteine, aspargine and glutamine acids, serine, proline, glicyne and alanine.
Analysis of the obtained results showed that mineral fertilization much more differentiate the content of
amino acids in maize than the organic treatment. In the case of organic fertilization the highest total content of
amino acids in plant was obtained in the variant with a double dose of municipal sludge. The highest
concentrations of exogenic amino acids was registered in maize fertilized with a double NPK dose, the lowest
in plants fertilized with a single dose of compost. Among the exogenic amino acids leucine prevailed in the
yields from all fertilizer treatments. It was demonstrated that methionine was the limiting amino acid.
Keywords: amino acids, farmyard manure, compost, sewage sludges, NPK, maize
One of the important parameters of plant yield assessment is biological value of
protein determined on the basis of its amino acid composition [1, 2]. It has been
commonly known that the value depends primarily on the content of exogenic
(indispensable) amino acids, which animal organism cannot synthetize. The exogenic
amino acids for animals are: phenylalanine, leucine, isoleucine, lysine, methionine,
treonine, tryptophan, valine, histidine and arginine [3]. Insufficient content of even one
of the above-mentioned amino acids in animal feed causes that the other are not
1
Department of Agricultural and Environmental Chemistry, University of Agriculture in Krakow, al.
A. Mickiewicza 21, 31–120 Kraków, Poland, phone +48 12 662 13 41, fax +48 12 662 43 41, email:
[email protected]
546
Czes³awa Jasiewicz and Agnieszka Baran
assimilated by the organism at all or only to a small extent. The factors shaping both the
crop yield and the share of individual amino acids in plant protein include fertilization,
ie the kind and method of fertilizer application (mineral, natural or organic fertilizers)
and the amount of applied doses [4–6]. Rational mineral and organic fertilization
determines production of adequate quality yields and protects the soil and water
environment against degradation. Additionally, a deficit of organic fertilizers necessitates
the use of some wastes as unconventional fertilizers in agriculture [7]. According to
Mazur [8] and Sita and Wasiak [9] the management of organic, chemically and
biologically uncontaminated wastes in agriculture is of crucial importance for the
natural environment and ecology and is the most rational way of their utilization.
Undoubtedly, the important advantage of organic material is the fact that they contain
nutrients, crucial for plants, are good substrate for soil humus formation, whereas their
fertilizer effect, especially in case of compost, is prolonged in time [10]. The paper
aimed at an assessment of mineral and organic fertilization on the composition of amino
acids in maize.
The investigations of the effect of mineral and organic fertilization on amino acid
composition in maize were conducted as a pot experiment. Maize (Zea mays L.), San
c.v. was the test plant. The experiment was set up on the soil with granulometric
structure of weakly loamy sand and pHKCl 4.66. The analyzed soil contained: 11.2
g × kg–1 organic carbon, 1.0 g × kg–1 nitrogen, 7.2 mg P2O5 × kg–1 and 17.3 mg K2O × kg–1
d.m. The experimental design comprised 11 treatments in four replications differing
with a dose and kind of supplied fertilizers (Table 2). The source of nutrients were:
mineral salts, farmyard manure, compost, municipal and industrial sewage sludge. Two
doses of NPK fertilization were considered in the experiment. On dose I 0.55 g N, 0.22
g P, 0.52 g K × pot–1 were used, dose II corresponded to 1.10 g N, 0.44 g P and 1.04 g
K × pot–1. Doses of farmyard manure, compost, municipal and industrial sewage sludge
were determined on the basis of nitrogen fertilization assumed for mineral treatments.
Table 1
Chemical composition of organic materials
Chemical composition
Dry mass
%
Organic mater
C-Organic
N
g × kg–1 d.m.
Farmyard
manure
Compost
Municipal
sludge
Industrial
sludge
14.56
54.72
18.81
21.84
855.3
437.3
640.4
482.8
413.6
253.60
371.47
280.0
20.9
26.40
40.10
28.80
P
4.50
5.10
16.00
8.60
K
19.70
13.40
3.50
2.30
g × pot–1
1/2 dose
181.0/362.0
38.0/76.0
73.0/146.0
87.4/174.9
Comparison of the Effect of Mineral and Organic Fertilization...
547
Technical NPK salts were supplied as water solutions of NH4NO3, KH2PO4 and KCl.
Chemical composition and the doses of applied fertilizer components were presented in
Table 1. Compost was manufactured from plant wastes by Ekokonsorcjum Efekt Ltd. in
Krakow, whereas sewage sludges originated from “Empos” municipal-industrial sewage
treatment plant in Oswiecim. Exceeded heavy metal concentrations were determined
neither in compost nor in sludges, therefore these materials met the requirements for the
fertilizers used in agriculture and land reclamation for agricultural purposes [11].
Harvesting maize was after 63 days vegetation in 8–10 leaves phase. After harvesting
the plant material was dried and dry mass yield was assessed, as well as total N and
protein N using Kjeldahl distilling method [12]. Amino acids were determined with
ninhydrine method by AA-400 Ingos analyzer. Determined were 17 amino acids:
theronine (Thr), leucine (Leu), phenyalanine (Phe), histidine (His), lysine (Lys),
methionine (Met), arginine (Arg), valine (Val), isoleucine (Ile), tyrosine (Tyr), cysteine
(Cys), aspargine (Asp) and glutamine (Glu) acids, serine (Ser), proline (Pro), glicyne
(Gly) and alanine (Ala).
Total contents of exogenic and endogenic amino acids in maize were presented in
Table 2.
Table 2
Scheme of experiment and total amino acids content in the maize aboveground parts
Amino acids sum
Egzogenic
Treatments
Endogenic
Egzogenic + Endogenic
mg × g–1 d.m.
I
Without fertilization
13.31
16.92
30.23
II
NPK*
21.97
25.90
47.87
III
NPK**
27.83
35.97
63.80
IV
Farmyard manure*
14.14
16.41
30.55
V
Farmyard manure**
15.04
17.20
32.24
VI
Compost*
13.66
17.73
31.39
VII Compost**
15.50
15.09
30.59
VIII Municipal sludge*
16.00
18.25
34.25
IX
Municipal sludge**
20.81
23.96
44.77
X
Industrial sludge*
16.88
18.98
35.86
XI
Industrial sludge**
17.97
20.71
38.68
* dose I: 0.55 g N × pot , ** dose II: 1.10 g N × pot .
–1
–1
Percentage use of exogenic amino acids fluctuated from 44 % to 51 % depending on
the treatment, whereas endogenic amino acids content was slightly higher and
constituted between 49 % and 56 % of the total sum of these compounds. It was
demonstrated that the applied fertilization affected an increase in amino acid sum
548
content in maize as compared with the control treatment. However, mineral fertilization
contributed to the increase in endogenic and exogenic animo acids sum more than
organic fertilization. Additionally, higher contents of amino acids were found in the
treatments with the second fertilization level than the first. In the treatment with
a double NPK dose both the contents of exogenic and endogenic amino acids raised
over twice in comparison with the control. In case of organic treatment, the highest
contents of exogenic and endogenic amino acids in maize were noted in treatments
fertilized with a double dose of municipal sludge (Table 2). This increase was 56 % in
relation to the control (for exogenic) and 42 % (endogenic) amino acids. The smallest
content of amino acids was registered in biomass maize cultivated in treatment with a
single dose of compost. Additionally on treatments receiving farmyard manure and
compost, the contents of amino acids were on a similar level. Moreover, these fertilizers
caused a slight increase in the content of amino acid sum, on average by 4 %
(I fertilization level) and by 15 % (II level) in comparison with the unfertilized control.
Depending on the fertilizer treatment, the total contents of amino acid sum in maize
may be put in the following order: farmyard manure » compost < industrial sewage
sludge < municipal sewage sludge < NPK.
Irrespective of the experimental treatment, leucine prevailed among the exogenic
amino acids constituting on average 20 % of their total sum (Table 3).
Table 3
Egzogenic amino acid content in the maize aboveground parts
Thr
Leu
Ile
Phe
Treatments
His
Lys
Met
Arg
Val
1.89
mg × g d.m.
–1
I
1.29
2.80
1.26
1.30
1.16
1.67
0.30
1.67
II
NPK*
2.33
4.29
2.07
2.30
1.68
2.71
0.56
3.11
2.92
III
NPK**
3.13
5.34
2.51
3.01
2.06
3.47
0.78
3.94
3.59
IV
Farmyard manure*
1.50
2.86
1.30
1.38
1.18
1.76
0.43
1.85
1.88
V
Farmyard manure**
1.56
3.03
1.44
1.49
1.25
1.85
0.41
1.96
2.05
VI
Compost*
1.38
2.85
1.31
1.30
1.14
1.68
0.36
1.79
1.85
VII Compost**
1.58
3.15
1.43
1.48
1.30
1.88
0.44
2.17
2.07
1.67
3.24
1.49
1.54
1.41
1.92
0.48
2.11
2.14
IX
Municipal sludge**
2.14
4.17
2.02
2.08
1.68
2.53
0.53
2.83
2.83
X
Industrial sludge*
1.74
3.43
1.63
1.66
1.41
2.02
0.48
2.21
2.30
XI
Industrial sludge**
1.92
3.70
1.60
1.82
1.54
2.28
0.43
2.35
2.33
* dose I: 0.55 g N × pot–1, ** dose II: 1.10 g N × pot–1.
It was demonstrated that methionine was the amino acid limiting protein value.
Percentage use of Met in total contents of exogenic amino acids was 3 %. Percentage of
exogenic amino acids in the amino acids sum were as follows: Leu (20 %) > Arg (13 %)
» Val (13 %) > Lys (12 %) > Thr (10 %) » Phe (10 %) >Ile (9 %) > Hist (8 %) > Met
(3 %). Higher content of individual exogenic amino acids was registered in minerally
than in organically fertilized maize, but the treatments receiving a double NPK dose had
549
the highest contents of the analysed amino acids. On the other hand, while estimating
the organically fertilized treatments, the highest content of treonine and leucine in maize
were found on the treatments where a double dose of municipal sewage sludge was
used, whereas the greatest amounts of the other exogenic amino acids were noted in
maize fertilized with a double dose of municipal sewage sludge. Moreover, slightly
lower contents of individual exogenic amino acids were assessed in maize fertilized
with farmyard manure and compost than with sewage sludges (Table 3).
The contents of analyzed endogenic amino acids in maize were presented in Table 4.
As regards the endogenic amino acids the highest content in maize was registered for
glutamine acid, which made up 23 % of the total content of endogenic amino acids. The
contents of endogenic amino acids may be put in the following order: Glu (23 %) > Asp
(18 %) > Ala (16 %) > Pro (14 %) > Gly (10 %) > Ser (9 %) > Tyr (7 %) > Cys (3 %).
Higher content of individual endogenic amino acids was found in maize fertilized with a
double NPK dose. On the other hand, among the organically fertilized treatments, maize
cultivated on the treatment with a double dose of municipal sewage sludge revealed the
highest content of the analyzed amino acids (Table 4). Compost applied in a single dose
affected a decrease in the content of analyzed amino acids from 9 % to 29 % in relation
to the control.
Table 4
Endogenic amino acid content in the maize aboveground parts
Asp
Ser
Glu
Treatments
Pro
Gly
Ala
Tyr
Cys
mg × g d.m.
–1
I
3.03
1.58
3.83
2.25
1.77
2.75
1.20
0.51
II
NPK*
4.81
2.34
5.81
3.75
2.62
4.21
1.71
0.65
III
NPK**
7.85
3.44
7.86
4.93
3.55
5.58
1.93
0.83
IV
Farmyard manure*
2.91
1.55
3.74
2.28
1.73
2.67
1.11
0.42
V
Farmyard manure**
3.06
1.62
3.88
2.41
1.82
2.86
1.15
0.36
VI
Compost*
2.73
1.43
3.45
1.95
1.61
2.51
1.05
0.40
VII Compost**
3.19
1.69
4.09
2.34
1.86
2.91
1.18
0.47
0.49
3.25
1.72
4.08
2.59
1.92
2.92
1.28
IX
Municipal sludge**
4.42
2.18
5.34
3.62
2.45
3.86
1.54
0.55
X
Industrial sludge*
3.43
1.73
4.30
2.52
2.04
3.13
1.33
0.50
XI
Industrial sludge**
3.82
2.04
4.80
2.61
2.23
3.37
1.27
0.57
* dose I: 0.55 g N × pot–1, ** dose II: 1.10 g N × pot–1.
Fertilization greatly affects the structure of yields and considerably modifies the
contents of amino acids in plants [13, 14]. Research conducted by Nowak and
Majcherczak [14] demonstrated that application of only mineral fertilization leads to
a decline in the contents of majority of amino acids in plant total protein in comparison
with treatment unfertilized with NPK or farmyard manure. In the studies of Czuba and
Mazur [15] exogenic amino acid contents decreased in result of nitrogen fertilization,
except for phenylalanine and leucine. Nitrogen fertilization also contributes to decreas-
550
ing lysine content [16]. On the other hand Domska et al [2] found a higher content of
exogenic amino acids in protein of barley grain under the influence of organic-mineral
fertilization with copper and zinc supplement. The research of Jasiewicz et al [17]
revealed that plants fertilized with various materials and organic wastes contained much
more exogenic amino acids than those receiving mineral fertilizers, however leucine
prevailed on all treatments. In the presented experiment a higher content of exogenic
and endogenic amino acids was registered in maize fertilized minerally (a single and
double NPK dose) than organically. The similar examination received in content of total
and protein nitrogen in maize, presented in the previous publication [12]. It was also
showed that higher contents of these parameters in minerally than organically fertilized
plants. Moreover, as has been emphasized in the introduction, feed protein value is
primarily determined by its composition of amino acids. In view of nutritional value, a
group of amino acids indispensable for animal organisms (exogenic) has been identified
in proteins. Among them the most important are limiting amino acids, ie those whose
amounts are the lowest in relation to animal needs, these include lysine and methionine
[3]. According to Rogalski [18] protein of grasses used for fodder reveals considerable
deficiency of methionine and the content of this amino acid limits its value. Presented
research also found that maize on all fertilizer treatments revealed the lowest content of
this amino acid.
Conclusions
1. Mineral fertilization affected an increase in the total contents of amino acids to
a greater degree in comparison with organic fertilization and control treatment.
2. In case of organic fertilization the highest total contents of amino acids in the
maize aboveground parts was obtained in the variant with a double dose of municipal
sludge.
3. The highest content of exogenic and endogenic amino acids in maize was
registered on treatments fertilized with a double NPK dose and the lowest in plants
receiving a single dose of compost.
4. Leucine prevailed among all exogenic amino acids in the protein maize
aboveground parts from all fertilizer treatments, whereas glutamine acid among the
endogenic amino acids.
5. It was demonstrated that methionine was the amino acid limiting protein value.
References
[1] Nowak K. and Majcherczak E.: Zesz. Probl. Post. Nauk. Roln. 2002, 484, 441–449.
[2] Domska D., Wojtkowiak K., Warechowska M. and Raczkowski M.: Zesz. Probl. Post. Nauk. Roln.
2003, 494, 99–104.
[3] Jamroz D. (ed.): ¯ywienie zwierz¹t i paszoznawstwo, Cz. III. Wyd. Nauk. PWN, Warszawa 2001,
pp. 407.
[4] Czuba R.: Zesz. Probl. Post. Nauk Roln. 1996, 440, 65–73.
[5] Klupczyñski Z.: Wp³yw nawo¿enia azotem na plon i jakoœæ ziarna zbó¿. Mat. Symp.: Wp³yw nawo¿enia
na jakoœæ plonów, 24–25 VI 1986, Olsztyn, 82–102.
[6] Mazur T. and S¹dej W.: Zesz. Probl. Post. Nauk. Roln. 2002, 484, 377–384.
551
[7] Mazur T.: Zesz. Probl. Post. Nauk Roln. 1999, 467, 151–157.
[8] Mazur T.: Acta Agrophys. 2002, 70, 257–263.
[9] Siuta J. and Wasiak G.: Zasady wykorzystania osadów œciekowych na cele nie przemys³owe (przyrodnicze). In¿. Ekol. 2001, 3, 13–42.
[10] Gambuœ F. and Wieczorek J.: Zesz. Probl. Post., Nauk Roln. 1999, 467, 513–520.
[11] Rozporz¹dzenie Ministra Œrodowiska z dnia 1 sierpnia 2002 r. w sprawie komunalnych osadów
œciekowych. DzU. nr 134, poz. 1140.
[12] Jasiewicz Cz. and Antonkiewicz J.: Wp³yw dawki i rodzaju nawozu na zawartoœæ azotu w kukurydzy.
Mat. Pokonf.: Zanieczyszczenia œrodowiska azotem. Monografie Wszechnicy Mazurskiej w Olecku,
Olsztyn 2005, 143–152.
[13] Majcherczak E., Cwojdziñski W. and Nowak K.: Acta Sci. Polon., Agriculture 2003, 2(2), 11–18.
[14] Cwojdziñski W. and Nowak K.: Zesz. Nauk. AR Szczecin 2000, 211, 63–84
[15] Czuba R. and Mazur T.: Wp³yw nawo¿enia na jakoœæ planów. Wyd. Nauk. PWN, Warszawa 1988.
[16] Krasnodêbska I. and Korelewski J.: Rocz. Nauk. Zootech. 1975, 2(2), 209–219.
[17] Jasiewicz Cz., Antonkiewicz J. and Baran A.: Zesz. Probl. Post. Nauk Roln. 2006, 513, 149–159.
[18] Rogalski M. (ed.): £¹karstwo. Wyd. Kurpisz, Poznañ 2004, pp. 271.
PORÓWNANIE WP£YWU MINERALNEGO I ORGANICZNEGO NAWO¯ENIA
NA SK£AD AMINOKWASÓW W ZIELONEJ MASIE KUKURYDZY
Katedra Chemii Rolnej i Œrodowiskowej
Uniwersytet Rolniczy im. Hugona Ko³³¹taja w Krakowie
Abstrakt: Celem badañ by³a ocena wp³ywu nawo¿enia mineralnego i organicznego na sk³ad aminokwasów
w kukurydzy odmiany San. Badania prowadzono w warunkach doœwiadczenia wazonowego. Schemat doœwiadczenia obejmowa³ 11 obiektów ró¿ni¹cych siê dawk¹ oraz rodzajem wprowadzonych nawozów.
Stosowano dwa poziomy nawo¿enia NPK. Jako Ÿród³o sk³adników pokarmowych dla kukurydzy zastosowano
sole mineralne (NPK), obornik, kompost, osad œciekowy miejski i przemys³owy. Dawki obornika, kompostu
oraz miejskiego i przemys³owego osadu œciekowego ustalono na podstawie poziomu nawo¿enia azotowego
przyjêtego w obiektach z nawo¿eniem mineralnym. Oznaczono 17 aminokwasów: treoninê, leucynê,
fenyloalaninê, histydynê, lizynê, metioninê, argininê, walinê, izoleucynê, tyrozynê, cysteinê, kwas asparaginowy i glutaminowy, serynê, prolinê, glicynê i alaninê. Analizuj¹c otrzymane wyniki stwierdzono, ¿e
nawo¿enie mineralne w wiêkszym stopniu ró¿nicowa³o zawartoœæ aminokwasów w kukurydzy w porównaniu
z nawo¿eniem organicznym. W przypadku nawo¿enia organicznego najwiêksz¹ zawartoœæ ogóln¹ aminokwasów w roœlinie uzyskano w wariancie z osadem miejskim zastosowanym w podwójnej dawce. Najwiêksz¹
zawartoœæ aminokwasów egzogennych stwierdzono w kukurydzy nawo¿onej podwójn¹ dawk¹ NPK,
najmniejsz¹ zaœ w roœlinach nawo¿onych kompostem w pojedynczej dawce. Spoœród aminokwasów egzogennych w plonach ze wszystkich obiektów nawozowych przewa¿a³a leucyna. Wykazano, ¿e aminokwasem
limituj¹cym by³a metionina.
S³owa kluczowe: aminokwasy, obornik, kompost, osady œciekowe, NPK, kukurydza
A
Vol. 18, No. 4
2011
Andrzej KOCOWICZ1 and El¿bieta JAMROZ1
CARBON AND NITROGEN CONTENT
OF MOUNTAIN MEADOW AND FOREST PODZOLS
AND BROWN ACID SOILS
ZAWARTOŒÆ WÊGLA I AZOTU
W BIELICOWYCH I BRUNATNYCH GLEBACH GÓRSKICH
POD U¯YTKOWANIEM DARNIOWYM ORAZ LEŒNYM
Abstract: On Karkonosze Mts area investigation on some soil forming factors influence on total nitrogen
content and C/N ratio of soil were conducted. The objects of researches were forest and meadow brown acid
soils and podzols. Soil profiles were developed from granites and mica slates and localized in altitude range
650–1350 m a.s.l. The soils had texture of clay sands, very acid and acid reaction, high hydrolytic acidity and
high content of carbon and nitrogen and high C/N ratio. Higher value of C/N ratio and carbon content of O
and Bbr horizon was determined in the forest soils than in the meadow soils. The investigations showed
influence of soil parent rock on carbon content of Bbr, Ees, Bhfe and C horizons. Soils developed from mica
slates had higher carbon content than soils developed from granites. The influence of climatic condition were
revealed in Bbr and parent rock horizons. Content of carbon and nitrogen which raised along with the altitude
up to 1100 m a.s.l. Above 1160 m a.c.l. decrease of C/N ratio in O horizon has been observed.
Keywords: mountains soils, nitrogen, C/N ratio, vegetation, climatic condition, parent rock
Organic matter is one of the most important components of soil. Even though that
usually is only small part of soil has influence on almost every soil proprieties and
plants supply in nutrients. Research on organic matter distribution and transformation is
possible by examination of the main components of organic matter – carbon and
nitrogen. Equally relation between carbon and nitrogen content which is described as
C/N ratio is very important. This indicator characterizes the organic matter transformation and describes indirectly many processes running in soils. Content of carbon,
nitrogen and C/N ratio in soils depends on many factors but especially on soil forming
factors. Convenient regions to conduct investigations on soil forming factor are
1
Institute of Soil Sciences and Environmental Protection, Wroc³aw University of Environmental and Life
Sciences, ul. Grunwaldzka 53, 50–357 Wroc³aw, Poland, phone: +48 71 320 56 40, fax: +48 71 320 56 31,
554
Andrzej Kocowicz and El¿bieta Jamroz
mountains because in small area is possible to examine very different environmental
condition. On the other side influence of man’s activity on soil is relatively minor.
The considerable range of altitudes, the large variability of soil parental material and
different vegetation in relatively small area enables to study climatic condition, parent
rock and vegetation influence on soil properties.
Investigations were conducted on Karkonosze Mts (western Sudeten) area (Fig. 1).
32 profiles of mountain soil were selected. The soil profiles were situated in four
perpendicular to contour line transects on northern slopes of mountains. Two transects
was set on soils developed from granites and two on soils developed from mica slates.
These rocks differ in texture, structure and resistance to weathering process as well as
weathering products [1]. These attributes diversify mechanical and physical proprieties
of rocks and residuum. Within the transects four altitude ranges (1–4) were set:
650–720, 820–900, 1000–1100 and 1160–1350 m a.s.l. (Table 1). The main differences
between altitude ranges are climatic conditions. The most important were temperature
and humidity (Table 2). These factors diversified water distribution of the soils,
intensity of eluvial and weathering processes and organic matter transformations.
Fig. 1. Localization of investigated soils
The soils profiles were set parallel, in pairs under meadow and forest vegetation. On
the meadow soils predominant species was Calamagrostis villosa and Deschampsia
flexuosa, above 1000 m a.s.l. Nardus stricta. The spruce Picea abies on forest soils was
the main species, while at zone of forest upper limit the was dwarf mountain pine Pinus
montana.
In the range of height up to 900 m a.s.l. only brown acid soils were present, in the
range from 1000 to 1100 m a.s.l. brown acid soil and podzols were found, and above
1160 m a.s.l. only podzols.
Carbon and Nitrogen Content of Mountain Meadow and Forest Podzols...
555
Table 1
Reaction, Hydrolitic acidity of soils Karkonosze Mts soils
Properties
pH
O
A
Bbr
Ees
H2O
3.67
3.97
4.44
KCl
3.32
3.53
3.97
12.85
9.18
6.17
Hh
Bhfe
C
4.03
4.2
4.51
3.49
3.74
4.14
7.88
8.33
4.38
Table 2
Fraction composition of soils of Karkonosze Mts
Fraction
[mm]
Soil horizons
Soils developed from
A and Ees
Bbr Bhfe
C
granites
1–0.01
47.4
49.8
48.6
50.9
mica slates
44.6
0.1–0.02
37.5
35.1
33.6
31.3
40.7
< 0.02
15.1
15.1
17.8
17.8
14.7
< 0.002
1.9
2.2
1.8
1.9
1.9
The samples of the soils were taken from every genetic horizon. The following
analyses in fraction below 1 mm were conducted: total organic carbon – Ctot with Tiurin
method, total nitrogen – Ntot with Kjeldahl method, pH with potentiometer in H2O and
1 M × dm–3 KCl solution, hydrolytic acidity (Hh) with Kappen method [2]. Average
values of O, A and C horizons from all soil profiles for were calculated, for Bbr horizon
from brown acid soil and for Ees and Bhfe horizons from podzols. Individual data for
average values calculation were chose on the basis of the soil horizons morphology.
Statistical analyses were executed at significance level 0.95 with Statistica 9.0.
The texture of presented soils was clay sands with high content of silts and skeleton
(Table 3). Minor differences were connected with depth of horizons and between soil
developed from various rocks. The hydrolytic acidity was high, reaction very acid and
acid (Table 4). The soils were developed from diluvial-weathered material.
Table 3
Climatic condition of Karkonosze Mts. area (Kwiatkowski, Ho³dys 1985) [20]
Altitude
[m a.s.l.]
Mean annual
temperature
[oC]
Annual sum
of percipitation
[mm]
640
5.8
1158
83–118
872
4.0
1233
115–128
1077
3.7
1349
126–134
1331
1.9
1429
136–155
Days with temperature
below 0
[oC]
556
Table 4
Total carbon (Ctot) and nitrogen (Ntot) content and C/N ratio of meadow
and forest soils of Karkonosze Mts
C
N
C/N
Soil
horizon
C
N
C/N
%
Meadow soils
Forest soils
O
38.29
1.76
21.70
40.97
1.69
A
6.75
0.43
15.31
6.55
0.40
24.54
18.05
Bbr
3.21
0.21
a 14.74 a
4.51
0.25
a 18.91 a
Ees
2.64
0.17
14.08
2.53
0.22
14.27
Bhfe
4.80
0.31
15.39
3.99
0.22
17.96
C
1.70
0.13
12.91
1.95
0.13
14.77
Values differing signifficantly between vegetation were marked with the same letter.
Content of Ctot and Ntot of examined soil was high. Moreover this elements were
present in every soil horizon including parent-rock horizon (Table 5–7). High content of
organic matter is mountain soils attribute [3–6]. This characteristic is connected mainly
with climatic condition of mountain areas – low temperatures and large precipitation
what promotes organic matter accumulation. Content of Ctot and Ntot of investigated
soils decreased in depth of profiles. Simultaneously process of organic matter
eluviations from Ees horizon to Bhfe horizon took places, what resulted in reduction of
Ctot and Ntot content in Ees horizons and increase in the Bhfe horizon.
The C/N ratio was high, what is typical for poor mountains sites. The high level of
this indicator is connected with character of the organic matter of mountain environment, slow rate of organic matter mineralization as well as low pH of soil and high
hydrolytic acidity [6–8]. Very significant was severe mountain climate condition which
is not favorable for biological activity. C/N ratio were the highest in organic horizons
and decreased in depth of the soils. Similar tendency observed Drozd [3], Drozd et al
[4], Licznar and Mastalska-Cetera [5], Skiba [6], Drewnik [7]. C/N ratio was lower in
albic horizons and higher in spodic horizons (Table 5–7) as effect of podzolization
process.
The influence of vegetation on Ctot content and C/N ratio in soil was observed. Forest
soils had higher content of Ctot than meadow soils in O, Bbr and C horizons but not
statistically significant (Table 5). Higher content of Ctot in forest soils than in meadow
soils has been reported by different researchers [5, 9–11]. Such regularity was not found
in soils Ees and Bhfe horizons of podzols. Reason for this could be to overbalance of
abiotic factor over biotic (vegetation influence) on the highest altitude range, where
podzols dominate. Moreover in the highest zone the forest ecosystem withdraw and
became more and more similar to meadow. Soils under meadow and forest had different
values of C/N ratio. Higher value of this index were determined in the forest soils than
in the meadow soils. The differences achieved significant level in Bbr horizon
(Table 5). This indicates higher resistance of organic matter of the forest soils for
mineralization. Similar results were reported by other researchers [5, 9, 12–14].
557
Table 5
Total carbon (Ctot) and nitrogen (Ntot) content and C/N ratio of soils developed
from granites and mica slates of Karkonosze Mts
C [%]
N [%]
Soil
horizon
C/N
Soils developoed from
granites
mica slates
granites
mica slates
granites
mica slates
O
43.43
37.73
1.89
1.6
22.82
23.95
A
7.38
6.97
0.45
0.38
16.32
17.86
Bbr
3.27
3.93
0.2
0.25
17.26
14.92
Ees
a 1.71 a
a 3.11 a
0.3
0.21
12.41
15.15
Bhfe
3.22
4.51
0.19
0.25
16.58
18.88
b 1.29 b
b 2.19 b
0.11
0.14
11.62
14.83
C
Values differing signifficantly between soil parential rock were marked with the same letter.
The investigations showed influence of the parent rock on Ctot content in soils. This
relation was evident in the deeper soil depth and soil horizons of lower level of organic
matter content. Origin of these horizons is mainly connected with abiogenic and only
subsidiary with biogenic processes The higher amount of Ctot was discovered in Bbr,
Ees, Bhfe and C horizons of soils developed from mica slates than from granites. These
differences of Ees and C horizons were statistically significant (Table 6). Connections
between parent rock and soil nitrogen transformation has been observed by Gonzalez-Prieto and Villar [15].
Table 6
Total carbon (Ctot) and nitrogen (Ntot) content and C/N ratio of soils
from different altitudes of Karkonosze Mts
Altitude range [m] above sea level m a.s.l. – (No of altitude range)
Soil
horizon
650–720 – (1)
820–900 – (2)
1000–1100 – (3)
Nt
C/N
Ct
Nt
C/N
Ct
Nt
O
41.58
1.76
23.82
39.64
1.62
23.50
42.00
1.66
26.14 f 37.02 1.85 20.32 f
A
6.16
0.35
18.09
6.19
0.44
15.06
5.85
0.40
14.21 f
Bbr
C
C/N
1160–1350 – (4)
Ct
3.07 a 0.19 c 15.57 2.98 b 0.17 d 17.30 5.03 a b 0.32 c d 16.11 f
1.19
0.08 e 13.37
1.74
0.12
14.21
2.38
0.17 e d 14.18 f
Ct
Nt
C/N
6.48 0.37 18.33 f
n.d
n.d.
n.d.
1.38 0.12 16.67 f
Values differing signifficantly between soil parential rock were marked with the same letter.
Many authors [3, 10, 11, 14, 16–19] reported about influence of weather conditions
on processes of organic matter in soil accumulation and transformation. They reported
that on elevated localizations of low temperature and substantial precipitation organic
matter content of soil is bigger than in areas localized lower where temperature is higher
and precipitation lesser.
The content of Ctot and Ntot of presented soils in Bbr and C horizons showed
tendency to growth along with the altitude up to 1100 m a.s.l. The increase were
820–900
m a.s.l.
650–720
m a.s.l.
Altitude
range
forest soil
meadow
soil
forest soil
meadow
soil
Vegetation
50.64
45.40
6.21
4.25
1.15
Of
Oh
A
ABbr
C
0.58
C
54.64
1.89
Bbr
Ol
3.76
37.60
53.54
A
AO
Ol
1.27
C
2.72
ABbr
2.22
6.21
A
Bbr
1.19
55.74
O
1.64
2Bbr
C
2.14
3.82
Ad
1Bbr
56.33
Ol
Soil
horizon
C
%
0.09
0.15
0.73
1.66
1.71
1.79
0.08
0.17
0.37
1.50
2.40
0.11
0.13
0.17
0.21
2.44
0.07
0.12
0.13
0.35
2.50
N
12.76
28.33
8.51
27.35
29.61
30.53
7.27
11.11
10.16
25.07
22.31
11.54
17.08
16.00
29.57
22.84
17.04
13.67
16.46
10.91
22.53
C/N
RBbrC
ABbr
AO
Ofh
Ol
C
Bbr
A
2.92
5.27
16.03
33.96
55.80
2.67
3.90
5.12
8.03
0.72
C
Ad
2.68
5.86
10.34
45.69
48.20
1.40
3.00
3.42
6.57
47.10
C
Bbr
A
Ah
Ofh
Ol
C
Bbrl2
Bbr
Ad
Ol
Soil
horizon
Soils developed from granites
%
0.18
0.29
1.05
1.90
2.04
0.18
0.24
0.33
0.44
0.08
0.12
0.29
0.53
1.71
1.92
0.08
0.17
0.18
0.52
1.90
N
16.21
18.37
15.27
17.90
27.35
14.83
16.07
15.72
18.22
9.06
22.59
20.42
19.44
26.75
25.10
17.50
17.65
18.60
12.69
24.79
C/N
1.16
C
Bhfe
Ees
AO2
AO1
Ofh
4.85
3.92
15.85
16.68
51.84
55.81
C
Ol
4.20
6.05
3.26
21.66
Bhfe2
Bhfe1
Ees
AO
52.84
2.43
C
Ol
2.84
1.94
3.96
19.29
32.84
53.54
0.18
0.70
0.86
2.85
5.54
Bhfe
Ees
A
Oh
Ofh
Ol
C
Bbr2
Bbr1
A
Ad
Soil
horizon
C
%
1.19
0.29
0.26
0.83
1.12
1.65
1.92
0.10
0.28
0.35
0.16
1.05
2.12
0.13
0.15
0.12
0.20
0.84
1.24
1.78
0.04
0.12
0.13
0.26
0.08
16.72
15.08
19.10
14.89
31.42
29.07
11.60
15.00
17.29
20.39
20.63
24.93
18.69
18.95
16.14
19.80
22.96
26.48
30.08
4.55
5.83
6.59
10.96
16.29
C/N
4.92
3.24
Bhfe2
6.99
3.41
6.84
21.17
39.20
55.57
1.02
1.36
3.20
5.27
13.21
56.03
3.18
4.17
7.28
8.29
36.20
43.20
4.99
6.06
10.91
C
C
Bhfe1
AEes
A
Oh
Ofh
Ol
C
BbrC
Bbr
Ad Bbr
AOd
Ol
BbrC1
BbrC1
ABbr
A
Ofh
Ol
C
ABbr
Ad
Soil
horizon
Soils developed from mica slates
0.34
N
Total carbon (Ctot) and nitrogen (Ntot) content and C/N ratio of soils of Karkonosze Mts
%
0.15
0.22
0.44
0.35
0.48
1.30
1.92
2.08
0.07
0.10
0.17
0.30
0.80
2.19
0.21
0.20
0.39
0.40
2.01
2.21
0.31
0.48
0.69
N
21.60
21.96
15.84
9.73
14.37
16.28
20.42
26.72
14.57
14.10
18.53
17.58
16.55
25.59
15.43
20.83
18.90
20.96
18.01
19.55
16.10
12.64
15.74
C/N
Table 7
558
1160–135
0 m a.s.l.
1000–110
0 m a.s.l.
Altitude
range
forest soil
meadow
soil
forest soil
meadow
soil
Vegetation
56.15
14.80
0.79
1.96
1.87
Ol
Ohd
Ees
Bh
Bfe
0.51
2.83
BbrC
C
5.03
ABbr
2.35
6.37
A
Bhfe
40.10
Oh
0.99
46.60
Ofh
Ees
55.74
Ol
34.60
3.54
Bbr
26.90
5.36
ABbr
OT
32.60
AO
POt
56.44
Ol
Soil
horizon
C
%
0.06
0.16
0.13
1.94
1.42
0.11
0.18
0.08
1.68
2.69
0.22
0.40
0.45
0.90
1.84
1.93
0.18
0.44
1.53
2.16
N
8.47
14.69
7.62
13.87
24.37
17.02
10.86
9.87
8.81
20.87
12.86
12.58
14.16
44.56
25.33
28.88
19.66
12.17
21.31
26.13
C/N
1.99
C
4.13
2.11
1.32
Bhfe
C
2.40
4.10
Bhfe
Ees
AEes
Ah
11.19
1.16
C
Ol
3.18
2.67
4.50
25.04
B
Ees
AEes
AO
53.59
2.16
Bhfe2
Ol
3.07
5.48
3.75
40.29
37.51
55.80
1.06
4.06
10.53
48.21
C
Bhfe1
Bh
AEes
Oh
Ofh
Ol
C
Bbr
Ahd
Ol
Soil
horizon
Soils developed from granites
%
0.13
0.14
0.21
0.14
0.21
0.69
1.79
0.10
0.20
0.18
0.26
1.74
2.31
0.18
0.19
0.20
0.23
0.26
1.67
1.95
1.99
0.13
0.30
0.53
2.01
N
10.15
14.56
19.37
17.68
19.11
16.18
53.46
11.60
15.65
14.47
17.53
14.42
23.20
11.06
11.57
15.31
23.97
14.23
24.18
19.21
28.04
8.15
13.53
19.87
23.99
C/N
Bhfe
Bh
Ees
AO
Of
C
Bhfe
Ees
A
AOd
Ol
C
Bhfe
Ees
Oh
Ofh
Ol
BbrC
ABbr
AOd
Ol
Soil
horizon
2.52
6.28
2.09
25.04
40.63
1.77
4.00
3.21
6.16
21.52
55.16
1.06
6.02
3.92
28.56
34.50
54.76
4.50
8.39
17.66
54.70
C
%
0.21
0.32
0.16
1.49
1.99
0.16
0.22
0.22
0.30
0.87
2.25
0.06
0.16
0.23
1.52
1.26
2.03
0.26
0.32
0.70
12.00
19.63
13.06
16.81
20.42
11.06
18.18
14.59
20.52
24.74
24.52
17.67
37.63
17.04
18.79
27.38
26.97
17.31
26.22
25.23
27.21
C/N
C
Bhfe2
Bhfe1
AhEes
AO
Ol
C
Bhfe
AhEes
AO
Ol
C
Bbr
Oh
Of
Ol
C
Bbr
ABbr
AOd
Soil
horizon
C
1.83
2.46
3.72
10.91
37.42
55.77
1.70
3.72
10.85
34.25
56.20
2.45
6.98
33.17
49.48
55.71
3.21
4.10
6.98
14.23
Soils developed from mica slates
2.01
N
%
0.11
0.19
0.26
0.61
1.99
2.09
0.14
0.15
0.59
1.55
2.19
0.14
0.45
1.33
2.13
2.27
0.24
0.23
0.42
0.73
N
16.60
12.83
14.37
17.91
18.82
26.68
12.14
24.72
18.35
22.14
25.66
17.53
15.50
24.94
23.23
24.54
13.38
17.57
16.63
19.55
C/N
Table 7 contd.
559
560
significant of Nt content in C horizons between the height zone 1 and 3 also in Bbr
horizon between the zones 1 and 3 as well as 2 and 3. Similarly content of Ctot in Bbr
horizons differed significantly between altitude range 1 and 3 as well as 2 and 3
(Table 7).
In the altitude zone 1160–1350 m a.s.l. content of Ctot in O horizons was smaller than
in lower altitudes (Table 7). The reason for this is more intensive elution of Ctot in
higher altitude than in lower because of bigger precipitation (Table 2). Equally on this
elevation C/N ratio was minor than in soils localized lower. This could be connected
with relatively lower eluviations of Ntot than Ctot. Significant influence of altitude on
C/N ratio in soils appeared in O horizons between altitudes 3 and 4.
Conclusions
1. Influence of vegetation appears in the C/N ratio Ctot content. Forest soils exhibit
the higher value of C/N ratio and higher Ctot content than meadow soils.
2. Influence of parent material on Ctot level has been found. Content of Ctot in soils
developed from mica slates was higher than in soils developed from granites. This
tendency appeared in Bbr, Ees, Bhfe and C soil horizons.
3. Effect of climatic factor appeared in content of Ctot, Ntot and C/N ratio. Content of
Ctot and Ntot were higher in Bbr and C horizon as well as C/N ratio of O horizons was
minor in soils localized in higher altitudes.
References
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Katalog. Wyd. IOŒ, Warszawa 1991, pp. 334.
[3] Drozd J.: Problemy ekologiczne wysokogórskiej czêœci Karkonoszy. Oficyna Wyd. Inst. Ekologii PAN,
Dziekanów Leœny 1995, 113–121.
[4] Drozd J., Licznar S.E. and Licznar M.: Zesz. Probl. Post. Nauk. Roln. 1993, 411, 149–158.
[5] Licznar S. and Mastalska-Cetera B.: Geoekolgiczne. Probl. Karkonoszy. Mat., vol. 1, Wyd. Acarus,
Poznañ 1998, 215–223.
[6] Skiba S.: Ocena wp³ywu imisji przemys³owych na gleby Karkonoszy. Problemy ekologiczne wysokogórskiej czêœci Karkonoszy. Ofic. Wyd. Inst. Ekologii PAN, Dziekanów Leœny 1995, 97–121.
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1987, 320 pp.
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Ossoliñskich, Wroc³aw 1985, 87–116.
ZAWARTOŒÆ WÊGLA I AZOTU W BIELICOWYCH
I BRUNATNYCH GLEBACH GÓRSKICH POD U¯YTKOWANIEM DARNIOWYM
ORAZ LEŒNYM
Instytut Nauk o Glebie i Ochrony Œrodowiska
Uniwersytet Przyrodniczy we Wroc³awiu
Abstrakt: Na terenie Karkonoszy prowadzono badania dotycz¹ce okreœlenia wp³ywu wybranych czynników
glebotwórczych na zawartoœæ azotu ca³kowitego i stosunku C/N w glebach. Obiektem badañ by³y gleby
³¹kowe i leœne nale¿¹cych do typu gleb brunatnych kwaœnych i bielic. Zlokalizowane zosta³y one w przedziale
wysokoœciowym 600–1350 m n.p.m. na granitach i ³upkach ³yszczykowych. Charakteryzowa³y siê sk³adem
granulometrycznym piasków gliniastych, kwaœnym i bardzo kwaœnym odczynem, wysok¹ kwasowoœæ
hydrolityczn¹. Mia³y du¿¹ zawartoœæ azotu, wêgla i wysoki stosunek C/N, które zmniejsza³y siê w g³¹b profili
gleb. Gleby leœne wykazywa³y wiêkszy stosunek C/N, a w poziomach O, Bbr i C zawiera³y wiêcej wêgla ni¿
gleby ³¹kowe. Wspó³zale¿noœæ pomiêdzy rodzajem ska³y macierzystej gleb a zawartoœci¹ wêgla zaznaczy³a
siê w poziomach Bbr, Ees, B, C – gleby wytworzone z ³upków ³yszczykowych zawiera³y go wiêcej ni¿ gleby
wytworzone z granitów. Wp³yw warunków klimatycznych uwidoczni³ siê w poziomach genetycznych Bbr
i C. Profile gleb po³o¿onych wy¿ej zawiera³y wiêcej azotu i wêgla ni¿ gleby zlokalizowane ni¿ej.
S³owa kluczowe: gleby górskie, azot, stosunek C/N, czynniki glebotwórcze
A
Vol. 18, No. 4
2011
Urij Anatoljevich MAZHAJSKIJ1, Tatjana Mihajlovna GUSEVA2,
Andrej Valerjevich ILJINSKIJ1, Svetlana Valerjevna ANDRIYANEC1
and Ekaterina Sergeevna GUSEVA3
INFLUENCE OF HEAVY METALS ON MICROORGANISMS
TAKING PART IN THE CIRCULATION
OF NITROGEN IN SOIL
WP£YW METALI CIÊ¯KICH NA MIKROORGANIZMY
UCZESTNICZ¥CE W OBIEGU AZOTU W GLEBIE
Abstract: Nowadays natural cycles of nitrogen have undergone essential changes. The number of heavy
metals polluting soil possess an oligodynamic effect (bactericidal ability) which may affect the process of
circulation of biophilic elements, first of all of nitrogen, appreciably. The programme of researches included
microbiological investigations in a model experiment with sod-podzol soil polluted with heavy metals. The
results of the model experiment showed that increasing of soil pollution with heavy metals led to decrease of
the quantity of Azotobacter and decrease of Clostridium bacteria’s ability for butyric fermentation till its full
loss, to inhibit of vital functions of ammonificating bacteria.
Keywords: heavy metals, soil, landscape, microorganisms, nitrogen
Microorganisms are elementary components of the biosphere. They are necessary
links in food chains because transformation of important chemical elements on the
Earth is carried on by biochemical activity of microorganisms. With the help of bacteria
the circulation of biogenic elements is carried on including nitrogen. Nitrogen is the
most important chemical elements. It is part of proteins, nucleic acids and chlorophyll.
Nitrogen compounds play an important role in the process of photosynthesis, metabolism, new cells’ formation. Nitrogen is irreplaceable in the forming of top-soil and its
fertility, in increasing of agriculture effectiveness. Anthropogenesis has affected natural
1
Russian Scientific-Research Institute of Hydrotechny and Melioration, Meshersky branch, Solotcha, 1a,
Ryazan, Russia, phone: 8 (4912) 288 205, fax: 8 (4912) 288 205, email: [email protected]
2
Microbiology Department, State Medical University, Lenin street 22, Ryazan, Russia, phone: 8 (4912)
253 820.
3
Department of German Languages and Teaching Methodology, Ryazan State University, Svoboda street
46, Ryazan, Russia, phone: 8 (4912) 281 314.
564
Urij Anatoljevich Mazhajskij et al
processes of biological fixation and migration of nitrogen appreciably. Nowadays
natural cycles of nitrogen have undergone essential changes.
On the one hand, intensification of farming leads to rapid decrease of humus and
nitrogen stores in soil, on the other hand, the entrance of heavy metals (HM) in the
environment has increased sharply which affects microorganisms taking part in
transformation of nitrogen compounds [1].
The number of HM polluting soil possess an oligodynamic effect (bactericidal
ability) which may affect the process of circulation of biophilic elements, first of all of
nitrogen, appreciably [2, 3].
The problem of soil pollution with HM is of current importance for Ryazan region
characterized by developed agriculture and intensive man-caused influence on the
environment.
Researches were conducted at an ecological range representing a large-scale model
of a closed drained strip of Oka-river basin’s left bank.
The programme of researches included microbiological investigations in a model
experiment with sod-podzol soil polluted with heavy metals (HM). During the
arrangement of a model experiment for coverage of the diapason of soil pollution from
admissible to extremely dangerous 3 variants were worked out which were based on the
total index of Zc pollution (its value corresponds to a certain category of pollution). The
level of pollution covered the range from admissible to extremely dangerous. HM were
introduced into soil in the following concentrations: 0.5 of their approximate admissible
concentration (AAC) (1 variant), 1.5 of AAC (2 variant), 4.5 of AAC (3 variant)
(Table 1).
Table 1
The scheme of the experiment
The variants of the experiment
(the content of heavy metals in soil [mg × kg–1])*
Metal
Control
(the initial soil)
1
(0.5 of AAC)**
2
(1.5 of AAC)
3
(4.5 of AAC)
Cu
10.8
154.2
484.2
1474.2
Zn
123.5
151.5
701.5
2351.5
Pb
40.0
120.0
440.0
1400.0
Cd
0.4
2.1
7.1
22.1
Zc
1
247.5
802.6
2467.9
1
admissable
2
reasonably
dangerous
3
dangerous
4
extremely
dangerous
The category
of pollution
* The content of HM in soil in variants is given without the background taken into account; ** ACC for sod-podzol soil.
Influence of Heavy Metals on Microorganisms Taking Part in the Circulation of Nitrogen...
565
In the variants of the experiment with different pollution levels the quantity of
aerobic and anaerobic and ammonificating bacteria was identified by means of standard
methods.
For revealing of Azotobacter the method of soil nubbs was used. Test soil was
moistened with sterile water till a paste-like condition, then with the help of a bacterial
loop it was put in Petri dishes (50 nubbs in each Petri dish) on Ashbi nutrient medium.
The Petri dishes were incubated in a thermostat at 37 oC during 4–6 days. After
incubating the quantity of the nubbs overgrown with mucous colonies of Azotobacter
was counted, the percentage of overgrowing was calculated.
For revealing of anaerobic nitrogen-fixing bacteria of Clostridium in the soil under
consideration the method of accumulative culture in liquid medium by Vinogradskij
was used. This method is qualitative, the conclusion about vital functions of nitrogen-fixing bacteria of Clostridium was made on the ground of the visual signs of their
growth. The nutrient medium was poured in test tubes with a high layer, then nubbs of
the soil under consideration was sowed and incubated at 80 oC during 10 minutes for the
purpose of removal of sporeless bacteria from the concomitant nitrogen-fixing ones.
The crops were incubated in anaerobe conditions at 37 oC during 2–3 days. Butyric
fermentation that appeared in elective conditions and followed by allocating of gas
bubbles was the evidence of the evolution of anaerobe cryptogamic bacteria. Glucose
that is a component of the Vinogradskij medium turns into butyric acid and carbonic
acid as the result of the vital functions of the anaerobes, a lot of froth appears in the test
tubes what was marked visually.
For revealing of ammonificating bacteria in the soil under consideration the method
of sowing from soil suspensions on meat peptone agar (MPA). The culture of
ammonificators was obtained by sowing of MPA soil nubbs in test tubes. Under the
plugs of the test tubes litmus paper for revealing of ammonia and paper sodden with
lead acetate for revealing of hydrogen sulphide were put. The crops were incubated in a
thermostat at 30 oC during 2–3 days. This method is qualitative, the change of the
colour of test paper defined visually was the evidence of vital functions of ammonificating bacteria [4].
Revealing of anaerobe nitrogen-fixing bacteria of Clostridium and ammonificating bacteria was held with the help of qualitative methods based only on visual
methods fixed with survey gear. The obtained data do not have graphical or tabular
presentation.
All the experiments had thrice-repeated replication, the obtained data in the
experiment of revealing of Azotobacter were exposed to computer processing.
Fertility and the ability of self-cleaning depends on microorganisms taking part in the
transformation of nitrogen compounds.
An Azotobacter is a freely-moving nitrogen-fixing bacteria. An Azotobacter consumes ammonium salts, nitrates(V), nitrates(III) and amino acids as the sources of nitric
566
nutrition. It is an active producer of bacteria, enriches soil with nitrogen, is capable of
assimilation of compounds oxidizing with difficulty [5–7].
Ready nutrient medium was sowed with nubbs of the soil under consideration.
Overgrown with phlegm nubbs was evidence of the presence of Azotobacter in soil. The
results of the researches are given in Fig. 1.
The quantity of nubbs overgrown with phlegm
49
50
45
40
30
35
28
30
25
20
15
10
0.6
5
0
Control
0.5 AAC
1.5 AAC
4.5 AAC
The concentration of heavy metals in the soil under discussion
Fig. 1. The dependence of an Azotobacter’s growth on the level of soil pollution with heavy metals
Consequently, decrease of the quantity of nubbs overgrown with phlegm is in inverse
negative relationship with the level of its pollution with heavy metals which is proved
by the value of the coefficient of correlation (r = –0.97). So the more concentration of
metals in soil is, the less bacteria are. If the concentration is 4.5 of AAC, the
Azotobacter is not practically identified. Consequently, such a concentration is
destructive for an Azotobacter. Clostridium pasteurianum is a nitrogen-fixing anaerobe
that connects molecular nitrogen only if there is no combined nitrogen [5, 8]. Test tubes
with nutrient medium were sowed with nubbs of soil containing heavy metals in
different concentrations (the control soil, 0.5 of AAC, 1.5 of AAC, 4.5 of AAC). The
presence of Clostridium pasteurianum was judged by turbidity of the medium and
allocation of gas bubbles that is formed while butyric fermentation. In the test tubes
with the control soil on the second or the third day after the sowing the medium grew
turbid and active allocation of gas bubbles was observed. This was evidence of the
presence of Clostridium pasteurianum.
In the test tubes that were sowed with the soil with such concentrations of heavy
metals as 0.5 AAC and 1.5 AAC the same processes were running and it also showed
the presence of bacteria Clostridium. But alongside with it the decrease of the intensity
of fermentation was noticed and it showed inhibition of a bacterium’s activity by heavy
metals. In the test tubes with the soil containing heavy metals in such a concentration as
567
4.5 from AAC the signs of butyric fermentation (turbidity of the medium, allocation of
gas bubbles) were not noticed in all the three replications. The results of the researches
are presented in the Fig. 2.
The quantity of the experimental test tubes
with the signs of butyric fermentation that is evidence
of activity of Cl. pasteurianum [%]
100
100
100
90
80
67
70
60
50
40
30
20
0
10
0
Control
0.5 AAC
1.5 AAC
4.5 AAC
Fig. 2. Dependence of the intensity of butyric fermentation caused by Cl. pasteurianum on the level of soil
pollution with heavy metals
There can be two reasons for it: pollution of soil with heavy metals blocked the
ability of bacteria for fermentation; pollution of soil with heavy metals leads to death of
Clostridium pasteurianum.
In the model experiment the influence of HM on ammonificating bacteria was
studied. In the process of ammonification of proteins aerobes (Bacillus mycoides,
B. megatherium, B. mesentericus, B. subtilis, B. prodigiosum and others), facultative
anaerobes (B. proteus vulgaris, E. coli) and anaerobes (Cl. putrificus, Cl. sporogenes)
took part [5, 7, 9].
The test tubes with nutrient medium were sowed with nubbs of soil polluted with
heavy metals in different concentrations (control, 0.5 of AAC, 1.5 of AAC, 4.5 of
AAC). Allocation of ammonia and hydrogen sulphide that were formed as a result of
putrefaction of proteins indicated the presence of bacteria. In the results of the
experiment it was found out that in the test tubes with the control soil and the soil with
heavy metals in such concentrations as 0.5 of AAC and 1.5 of AAC ammonia and
hydrogen sulphide allocated. Consequently, one can make a conclusion that ammonificating bacteria were present in the soil under consideration.
In the test tubes where the soil in the concentration 4.5 AAC was sowed gas did not
allocate and it is evidence of death of ammonificating bacteria. In the test tubes where
the soil with heavy metals in the concentration 4.5 AAC was sowed gas did not allocate
and presumably it was evidence of death of ammonificating bacteria. The results of the
researches are presented in the Fig. 3.
The quantity of the experimental test tubes
with the signs of ammonification of proteins
that is evidence of activity of ammonificating bactwria [%]
568
100
100
100
90
77
80
70
60
50
40
30
20
0
10
0
Control
0.5 AAC
1.5 AAC
4.5 AAC
Fig. 3. The dependence of the intensity of the process of ammonification of proteins on the level of soil
pollution with heavy metals
Conclusion
1. According to the results of a model experiment one can make a conclusion that
decrease of soil pollution with heavy metals leads to the decrease of the quantity of
Azotobacter.
2. The increase of the concentration of heavy metals in soil decreases the ability of
bacteria of Clostridium for butyric-acid fermentation till its complete loss.
3. The increase of heavy metals (HM) in soil leads to inhibition of vital functions of
ammonificating bacteria.
4. The results of the experiment carried out showed that if in sod-podzol soil of the
landscape of Oka-river’s left bank there are heavy metals in the amount exceeding
AAC, there is a real danger of the violation of nitrogen circulation and of the decrease
of soil fertility as a result.
References
[1] Dobrovolskij V.V.: The basis of biogeochemistry. The Publishing House “Academy”, Moscow 2003,
pp. 400.
[2] Lozanovskaja I.N., Orlov D.S. and Sadovnikova L.K.: Ecology and protection of the biosphere under
chemical pollution. The Higher School, Moscow 1998, pp. 287.
[3] Panin V.F., Sechin A.I. and Fedosova V.D.: Ecology for an engineer. The Publishing House
“Noosphere”, Moscow 2001, pp. 284.
[4] Zvjagintseva D.G.: Methods of soil microbiology and biochemistry. The Publishing House of MSU,
Moscow 1991, pp. 302.
[5] Netrusov A.I., Bonch-Osmolovskaja E.A. and Gorlenko V.M.: Ecology of microorganisms. The
Publishing House “Academy”, Moscow 2004, pp. 272.
569
[6] Sbojchakov V.B.: Microbiology with the fundamentals of epidemiology and methods of microbiological
researches. SnetsLit., Moscow 2007, pp. 592.
[7] Pozdeev O.K.: Medical microbiology. GEOTAR-Media, Moscow 2006, pp. 768.
[8] Vorobjev A.A., Krivoshein U.S. and Bykov A.C.: Fundamentals of microbiology, virology and
immunology. The Publishing House “Academy”, Moscow 2002, pp. 224.
[9] Vorobjev A.A., Krivoshein U.S. and Shirobokov V. P.: Medical and sanitary microbiology. The
Publishing House “Academy”, Moscow 2002, pp. 464.
WP£YW METALI CIÊ¯KICH NA MIKROORGANIZMY
UCZESTNICZ¥CE W OBIEGU AZOTU W GLEBIE
1
3
Rosyjski Naukowo-Badawczy Instytut Hydrotechniki i Melioracji, Riazañ, Rosja
2
Katedra Mikrobiologii, Riazañska Pañstwowa Akademia Medyczna, Rosja
Wydzia³ Jêzyków Germañskich i Metod Nauczania, Pañstwowy Uniwersytet w Riazaniu, Rosja
Abstrakt: W przyrodniczym obiegu azotu zaznaczy³y siê ostatnio istotne zmiany. Zanieczyszczenie gleby
metalami ciê¿kimi powoduje dzia³anie oligodynamiczne (zdolnoœæ bakteriobójcz¹), co mo¿e istotnie zachwiaæ
procesy obiegu pierwiastków biogennych, w pierwszej kolejnoœci azotu. Program badañ obejmowa³
mikrobiologiczne badania w eksperymencie modelowym z gleb¹ darniowo-bielicow¹ zanieczyszczon¹
metalami ciê¿kimi. Wyniki tego doœwiadczenia wykaza³y, ¿e zwiêkszenie zanieczyszczenia gleby metalami
ciê¿kimi prowadzi do zmniejszenia liczebnoœci, bakterii z rodzaju Azotobacter. Ponadto w przypadku bakterii
z rodzaju Clostridium wykazano obni¿enie zdolnoœci do przeprowadzenia fermentacji mas³owej, a¿ do pe³nej
jej utraty. Jednoczeœnie odnotowano zahamowanie ¿yciowych funkcji bakterii amonifikacyjnych.
S³owa kluczowe: metale ciê¿kie, gleba, krajobraz, mikroorganizmy, azot
A
Vol. 18, No. 4
2011
Zenia MICHA£OJÆ1
INFLUENCE OF VARIED DOSES AND FORMS
OF MICROELEMENTS AND MEDIUM
ON NITRATE(V) AND (III) CONTENT IN LETTUCE
WP£YW ZRÓ¯NICOWANYCH DAWEK I FORM MIKROELEMENTÓW
ORAZ POD£O¯A NA ZAWARTOŒÆ AZOTANÓW(V) I (III) W SA£ACIE
Abstract: Study carried out in 2005–2007 involving lettuce plants, the influence of varied doses and forms of
microelements as well as subsoil types on nitrates(V) and (III) contents was determined. Nitrates were
analyzed in fresh material by means of spectrophotometric method using Griess’s reagent. Lower nitrate(V)
concentration was found in plants cultivated in peat subsoil after applying basic (M1) rather than double (M2)
microelement dose. No significant influence of the form of applied microelements was recorded; instead,
considerable effect of their dose on nitrate contents at lettuce leaves was found. The tendency of decreasing
the nitrate concentration in plants along with the increase of organic substance content was also recorded.
Keywords: nitrate(V) and nitrate(III), lettuce, microelements dose and form, peat, sand, soil
Vegetables are an essential element of human diet and are the largest source of
nitrates(V) in food. According to FAO/WHO Expert Commission for Food Additives
(JECFA), the acceptable daily intake (ADI) for nitrates(V) is from 0 to 3.7 mg
NO3– × kg body weight daily and for nitrates(III) from 0 to 0.06 mg NO2– × kg body
weight daily [1]. Studies indicate that these limits are often exceeded [2–4]. Currently
obligatory maximum nitrates contamination levels for vegetables are set in the decree of
Commission Regulation (UE) No. 1881/2006 from 19th December 2006 [5]. The nitrate
contents in vegetables depends on genetic features as well as environmental and
agrotechnical conditions. Nitrate, potassium, and microelement nutrition is one of the
more important factors [6–9].
The present study aimed at evaluating the influence of varied doses and forms of
microelements as well as subsoil types on nitrate(V) and (III) contents in lettuce.
1
Department of Soil Cultivation and Fertilization of Horticultural Plants, University of Life Sciences in
Lublin, ul. Leszczyñskiego 58, 20–068 Lublin, Poland, phone: +48 81 524 71 26, fax: +48 81 524 71 25,
572
Zenia Micha³ojæ
The studies upon the lettuce (cv. Alanis) were carried out in 2005–2007 during the
spring cultivation cycle in a greenhouse in pots of 2 dm3 capacity. The cultivation
period since the seed sowing till the completing lasted about 60 days in all study years.
The experiment set in complete randomization pattern included 12 combinations. Each
combination was represented by 8 experimental units consisting of a single pot with
a single plant each.
Influences of the following factors were studied:
1. microelement forms: chelate or mineral;
2. microelement doses: basic – M 1, double – M 2;
3. subsoil type: peat – 85 % organic substance, soil + bark (v/v 3:1) 10 % organic
substance, sand – 0 % organic substance.
Microelements were applied in following forms:
– chelates: iron – 7.5 % Fe (50 % EDTA, 50 % DTPA), copper – 12 % Cu (100 %
EDTA), zinc – 14 % Zn (50 % EDTA, 50 % DTPA), manganese – 14 % Mn (50 %
EDTA, 50 % DTPA), molybdenum – Molibdenit 3.0 % Mo, boron – Bormax 11 % B;
– mineral forms: iron – FeSO4, copper – CuSO4 × 5H2O, zinc – ZnSO4 × 7H2O,
manganese – MnSO4 × H2O, boron – HBO3, molybdenum – ammonium molybdate.
Following microelement doses were applied (in mg × dm–3 subsoil):
– M 1 – Fe – 20; Cu – 12.2; Zn – 7.4; Mn – 5.1; Mo – 3.7; B – 3.2 (basic);
– M 2 – Fe – 40; Cu – 24.4; Zn – 14.8; Mn – 10.2; Mo – 7.4; B – 6.4 (double).
The acidity of all subsoils was adjusted to pH 6.5. The whole microelement and
phosphorus, 1/3 N, K, and Mg doses were applied during the pot filling with soil; the
remaining N, K, and Mg amounts were used post-crop every 7 days. The content of
nutritive components was sustained at the level of (in mg × dm–3): 150 N; 200 P; 300 K;
100 Mg. Considering the whole vegetation period, following quantities of elements
were applied (in g × plant–1): nitrogen (N) – 1.2 (in a form of KNO3 (13.5 %, 38 % K)
and NH4NO3 – 34 % N; phosphorus (P) – 0.4 in a form of (Ca(H2PO4)2 × H2O – 20.2 %
P); potassium (K) – 2.4 in a form of potassium nitrate (KNO3); magnesium (Mg) – 0.75
in a form of magnesium sulfate (MgSO4 × H2O – 17.4 % Mg, while microelements as
above. The moisture of subsoil was adjusted to the level of 70 %.
Contents of nitrates(V) and (III) were determined in fresh material directly after the
harvest by means of spectrophotometric method using Griess’s reagent according to
PN-92/A-75112 [10].
Results were statistically processed applying variance analysis. The difference
significance was verified on a base of t-Tukey’s multiple confidence intervals at the
significance level of a = 0.05.
Contents of nitrates(III) and (V) were determined in fresh leaves directly after lettuce
harvest. Achieved results were listed in Table 1 as well as Figs. 1–2. No univocal
dependence within nitrates(III) was found, because their concentrations oscillated from
Influence of Varied Doses and Forms of Microelements and Medium on Nitrate(V)...
573
Table 1
The content nitrate [mg NO3– × kg–1 f.m.] dependent microelements forms doses
and mediums in lettuce
Microelement
Kind of
medium
Years
Dose
2005
2006
2007
Average
for dose
M1
1349
2138
1664
1717
M2
1445
2358
1979
1927
M1
1030
1979
1664
1558
M2
1215
2338
1979
1844
1260
2203
1822
1762
M1
1349
2338
2024
1904
M2
1619
2158
1484
1754
M1
1619
2338
1979
1979
M2
1259
2158
1644
1687
1462
2248
1783
1831
M1
2148
2158
2159
2155
M2
1619
1619
1484
1574
M1
1990
1979
2519
2163
M2
1349
1879
1799
1676
Average for sand
1777
1909
1990
1892
Average for years
1499
2120
1864
Form
chelat
Peat
mineral
Average for peat
chelat
Soil + bark
mineral
Average for soil + bark
chelat
Sand
mineral
Total average
LSD0.05
1828
for dose – 119
for years – 202
for medium × dose – 380
for medium × years – 527
0 to 12 mg NO2– × kg–1 f.m. In majority of samples, there were trace amounts, thus those
results are not shown in the tables.
Content of nitrates (V) at lettuce leaves (cv. Alanis) was significantly differentiated
by the dose of applied microelements as well as dose and type of the subsoil. Regardless
of microelement form used, plants cultivated on peat revealed lower level of nitrates (V)
after applying basic (M1) than double (M2) microelement dose. In subsoil containing
£ 10 % of organic substance, adverse dependence was recorded (Table 1, Fig. 2). Such
results indicate that organic matter present in peat had a positive effect on nitrogen
conversion in plants. This dependence can be confirmed by studies [11, 12] that
revealed the greater nitrate(V) concentration in lettuce cultivated in sand, comparing
with mineral soil, with the same level of nitrogen in subsoil (150 mg N × dm–3).
Microelements were applied at the basic dose, that is commonly recommended for
plants cultivated under covering, and double one. Achieved results confirmed a
significant influence of applied microelement dose as well as the lack of considerable
effects of their form. Lower nitrate(V) contents was found at plants fertilized with the
double than basic microelement dose (Fig. 1). Therefore, present study prove that the
574
Zenia Micha³ojæ
1913
2 000
1744
1 800
mg NO3 × kg–1 f.m.
1 600
1 400
1 200
1 000
800
600
400
119
200
0
M1
M2
LSD0.05
Macroelement dose
Fig. 1. Content nitrate(V) (in NO3– × kg–1 f.m.) dependent doses microelements in lettuce (average for years
2005–2007)
peat
2 500
1941
mg NO3 kg–1 f.m.
2 000
soil + bark
sand
2159
1886
1721
1638
1625
LSD0.05
for dose – 182
for medium – 380
1 500
1 000
500
0
M1
M2
LSD0.05
Macroelement dose
Fig. 2. Content nitrate(V) (in mg NO3– × kg–1 f.m.) dependent microelements doses and mediums in lettuce
(average for years 2005–2007)
dose rather than form of applied microelements had greater influence on nitrate(V)
concentration. In research [13] it has been indicated that lettuce tolerates better the
deficit and overdose of microelements in peat rather than in mineral subsoil.
Furthermore, the optimal level of microelements in subsoil has been estimated.
There was no significant effect of subsoils with varied contents of organic matter on
nitrate level at lettuce plants. Although a tendency (Table 1) that the nitrate(V) content
at lettuce decreased along with the organic substance content increase in a subsoil was
apparent, their largest amounts were recorded in plants cultivated in sand, while the
Influence of Varied Doses and Forms of Microelements and Medium on Nitrate(V)...
575
smallest – in peat. Similar dependence was observed in study [6, 14] upon lettuce and
the subsoil influence on nitrate(V) contents.
Contents of nitrate were significantly differentiated when comparing results of
studies carried out in different years (Table 1). This can be explained with various
environmental conditions (light, its amount and intensity). Studies [8, 15] have also
revealed significant impact of these factors on nitrate(V) concentration in lettuce.
Conclusions
1. Regardless of the microelement form applied for plants cultivated in peat subsoil,
lower nitrates(V) content was recorded when basic (M1) rather than double (M2)
microelement dose was used.
2. No significant influence of the microelement form was found, instead their dose
appeared to have considerable impact on nitrate content at lettuce.
3. The tendency of decreasing the nitrate concentration at plants along with the
increase of organic substance content was recorded.
References
[1] JECFA: Joint FAO/WHO Expert Committee on Food Additives – Evaluation of certain food additives
and contaminants. World Health Organization 1995, 29–35.
[2] Ayaz A., Topeu A. and Yurttagul M. J.: Food Tech. 2007, 5(2), 177–179.
[3] Murawa D., Banaszkiewicz T., Majewska E., B³aszczuk B. and Sulima J.: Bromat. Chem. Toksykol.
2008, (1), 67–71.
[4] Tosun I. and Ustun N. S.: Bull. Environ. Contam. Toxicol. 2004, 72, 109–113.
[5] Dziennik Urzêdowy Unii Europejskiej, Rozporz¹dzenie Komisji Europejskiej (WE) NR 1881/2006 z 19
grudnia 2006, 364/15.
[6] Gonella M., Serio F., Conversa G. and Santamaria P.: Acta Horticult. 2004, 6(4), 61–67.
[7] Kozik E.: Acta Agrophys. 2006, 7(3), 633–643.
[8] Micha³ojæ Z.: Rozp. habilitacyjna, Wyd. AR Lublin 2000, 238, 5–65.
[9] Micha³ojc Z.: Zesz. Probl. Post. Nauk Roln. 2006, 513, 277–283.
[10] Polska Norma: Owoce, warzywa i ich przetwory. Oznaczanie zawartoœci azotanów i azotynów.
PN-92/A-75112.
[11] Huihe Li, Wang-Zhengyin and Li Baozhen.: Plant Nutr. Fertil. Sci. 2004, 10(5), 504–510.
[12] Safaa A. M. and Abd El Fattah M.S.: J. Appl. Sci Res. 2007, 3(11), 1630–1636.
[13] Tyksiñski W.: Rozp. habilitacyjna, Wyd. AR Poznañ 1992, 233, 5–62.
[14] Karimaei M.S., Massiha S. and Mogaddam M.: Acta Horticult. 2004, (644), 60–74.
[15] Kowalska I.: Folia Horticult. 1997, 9(2), 31–40.
WP£YW ZRÓ¯NICOWANYCH DAWEK I FORM MIKROELEMENTÓW
ORAZ POD£O¯A NA ZAWARTOŒÆ AZOTANÓW(V) I (III) W SA£ACIE
Katedra Uprawy i Nawo¿enia Roœlin Ogrodniczych
Uniwersytet Przyrodniczy w Lublinie
Abstrakt: W badaniach przeprowadzonych w latach 2005–2007 z sa³at¹ okreœlono wp³yw zró¿nicowanych
dawek i form mikroelementów oraz pod³o¿y na zawartoœæ azotanów(V) i (III) w liœciach sa³aty. Zawartoœæ
azotanów oznaczono w œwie¿ej masie roœlin metod¹ spektrofotometryczn¹ z odczynnikiem Griessa. Wykazano w roœlinach uprawianych tylko w pod³o¿u torfowym mniejsz¹ zawartoœæ azotanów(V) po zastosowaniu
576
Zenia Micha³ojæ
podstawowej dawki (M1) mikroelementów ni¿ podwójnej (M2). Stwierdzono brak istotnego wp³ywu formy
zastosowanych mikroelementów, natomiast wykazano istotny wp³yw ich dawki na zawartoœæ azotanów(V)
w sa³acie. Odnotowano tendencjê, i¿ wraz ze wzrostem zawartoœci substancji organicznej w pod³o¿u obni¿a³a
siê zawartoœæ azotanów(V) w roœlinach.
S³owa kluczowe: azotany(V) i (III), sa³ata, dawki i formy mikroelementów, torf, piasek, gleba
A
Vol. 18, No. 4
2011
Anna MIECHÓWKA1, Micha³ G¥SIOREK,
Agnieszka JÓZEFOWSKA and Pawe³ ZADRO¯NY
CONTENT OF MICROBIAL BIOMASS NITROGEN
IN DIFFERENTLY USED SOILS
OF THE CARPATHIAN FOOTHILLS
ZAWARTOŒÆ AZOTU BIOMASY MIKROBIOLOGICZNEJ
W RÓ¯NIE U¯YTKOWANYCH GLEBACH POGÓRZA KARPACKIEGO
Abstract: The paper presents results of studies on microbial biomass nitrogen content in agriculturally
managed soils of the Silesian and Ciezkowickie Foothills. We used soil material from 14 soil profiles located
in pairs – on adjoining arable lands and grasslands. In soil material was assessed the basic properties and
microbial biomass nitrogen by chloroform fumigation-extraction method. The analyzed soils were characterized by a high share of microorganism biomass nitrogen in its total content, which may evidence their high
biological activity. The contents of microbial biomass nitrogen and its share in the total nitrogen content in
grassland soils were significant higher than in arable soils. The content of microorganism biomass nitrogen in
the studied soils was positively correlated with the contents of total nitrogen and organic carbon, cation
exchange capacity and soil abundance in magnesium (available and exchangeable forms) and with
exchangeable sodium.
Keywords: Silesian and Ciezkowickie Foothills, soil management method, total nitrogen, microbial biomass
nitrogen
Microbial biomass constitutes a small quota of the soil organic matter, but due to its
considerable biochemical activity plays a major role in energy and nutrient cycling in
the ecosystems. The share of microbial biomass nitrogen in its total contents in arable
soils may be a sensitive indicator of the ecological balance in soils. Its values generally
fall within the 1–6 % range, and the higher the share, the “healthier” the soil [1]. It
results from a faster cycle of microorganism biomass circulation than the other organic
matter in soil [1, 2].
The content of microbial biomass nitrogen in soils depends on the physicochemical
and chemical properties of soils [2–8] and is related to the way of their use – the highest
in the forest soils, lower in grassland soils and the lowest in soils of arable lands [2, 9].
1
Department of Soil Science and Soil Protection, University of Agriculture in Krakow, al. A. Mickiewicza
21, 31–120 Kraków, Poland, phone +48 12 662 43 70, email: [email protected]
578
Anna Miechówka et al
In soils of arable land it is under the effect of the cultivation method [4, 7]. The impact
of fertilization and cultivation systems on the change of the level of the microbial
biomass nitrogen content is often analyzed basing on the results of field experiments [5,
7]. The content of carbon and microbial biomass nitrogen in the soils is also used for the
complete characterization of the soil environment of the same areas [2, 4, 8, 10]. In the
scientific literature there is a lack of such data for the agricultural soils of Carpathian
Foothills.
The paper aimed to determine the content of microbial biomass nitrogen and its share
in the total nitrogen content in the soils of the Silesian and Ciezkowickie Foothills and
the impact of soil management methods and some chemical and physicochemical
properties of investigated soils on changes of these parameters.
The paper used the soil material from 14 profiles of brown soils and soil lessives,
formed from the rock waste of the Œl¹sk unit, of the Carpathian Flysch localized in 7
sites (Table 1), in pairs – on adjoining arable lands and grasslands, so that when
comparing the analyzed soil properties it was possible to exclude the effect of soil
forming factors, other than the management method.
Table 1
Localization of analyzed soils
Localization
Longitude
Elevation
[m a.s.l.]
018o49¢14,3–15,7²E
379
No
Locality
Latitude
Silesian Foothills
1
Ustroñ
49o43¢18,7–19,5²N
o
2
Ustroñ
49 43¢25,5–25,6²N
018o49¢48,8–49,3²E
437
3
Górki Wielkie
49o46¢38,6–38,9²N
018o51¢15,8–15,9²E
353
4
Swoszowa
Ciezkowickie Foothills
5
Joniny
6
Czermna
7
Dobrocin
49o50¢27²N
021o11¢47,3²E
402
49 51¢12,6–13,8²N
021o11¢17,6–19,6²E
435
49o49¢10,1²N
021o19¢17,1²E
361
021o09¢58,7²E
416
o
o
49 50¢23,1²N
The information about the soil management methods were obtained from the farmers
cultivating them. Crop rotation: potatoes, wheat, cereal mixture (wheat, barley and oat)
was used on the arable lands, except for site 7 (potatoes, rye and oat). The soils were
fertilized every 2–3 years with farmyard manure and with mineral fertilizers, but much
lower doses of nitrogen fertilizers were applied on the Ciezkowickie Foothill (ca
10–30 kg N × ha–1) than on the Silesian Foothill (approximately 100–160 kg N × kg–1).
Lower nitrogen fertilization was recompensed by higher farmyard manure doses and on
the sites 4 and 5 additionally poultry manure was applied. On the grasslands mineral
fertilizers were used only on the sites: 3 (ca 100 kg N × kg–1), 4 (14 kg N × kg–1) and 6
Content of Microbial Biomass Nitrogen in Differently Used Soils...
579
(23 kg N × kg–1) and farmyard manure and (or) slurry on sites: 2 (the highest dose), 3
and 6. The grasslands on sites 1 and 7 were left unfertilized.
In the fine earth parts of the analyzed soils, texture was assessed using aerometric
Casagrande method in Proszynski’s modification [11], pH in H2O using potentiometric
method [12], the sum of exchangeable bases (BC) by means of determining individual
cations (Ca2+, Mg2+, K+ and Na+) after their extraction with 1 mol × dm–3 CH3COOHN4,
potential acidity (H+) with Kappen method using 1 mol × dm–3 CH3COONa for
extraction and the contents of: available phosphorus and potassium using Egner-Riehm
method, available magnesium with Schachtschabel method [13], total organic carbon
(TOC) with Euro Thermoglas TOC-TN 1200 apparatus, total nitrogen (TN) with
Kjedahl method by Kjeltec apparatus and microbial biomass nitrogen (BN) using
chloroform fumigation-extraction method [14].
The significance of differences between arithmetic means of selected properties of
corresponding arable soils and grasslands were assessed using Tukey test at significance
level p < 0.05. The value of correlation coefficient was also computed according to
Spearman’s rank order. The calculations were made using the STATISTICA program.
The analyzed soils were characterized by diversified texture, chemical and physicochemical properties, however in the surface horizons of grassland soils mean contents of
organic carbon, total nitrogen, microbial biomass nitrogen and available magnesium
were apparently higher, whereas average concentrations of available phosphorus and
potassium forms were lower than in the arable soils (Table 2, 3). Significant higher
contents of TOC, TN and BN in the grassland soils than in arable soils was in the first
place due to the fact that greater amount of organic biomass, processed by a greater
number of microorganisms was supplied to them [2, 5, 15]. Lower contents of available
P and K forms in the grassland soils can by connected with lower fertilization applied
on these lands in comparison with the plough lands, or with a total lack of fertilization
(Table 3). There are also higher average content of exchangeable base (except K+),
higher average potential acidity and average cation exchange capacity in the surface
horizons of grassland soils (Table 4).
Soil profiles, compared in pairs, representing arable lands and grasslands situated
close by, were approximate considering their morphology and some physicochemical
and chemical properties, particularly in lower situated genetic horizons. In the surface
horizons of these soils, some chemical properties became more or less diversified in
result of various methods of soil management and accompanying fertilization. On all
analyzed sites, the surface horizons of the grassland soils contained bigger amounts of
organic carbon, total nitrogen and microorganism biomass nitrogen than the analogous
soil horizons of the arable soils. These soils were also characterized by a higher share of
microorganism biomass nitrogen in its total content (Table 2). The highest differences
between the content of discussed components in arable soils and grassland soils were
assessed in soils from Czermna and Dobrocin villages (sites 6 and 7). The grassland
soils situated there contained almost 4 times more TOC, over twice more TN and
580
5 times more BN. These differences resulted from low contents of these components in
the arable soils (Table 2).
Table 2
Contents of total organic carbon (TOC), total nitrogen (TN) and microorganism biomass nitrogen (BN)
in surface horizons of analyzed arable soils and grasslands
Arable soils
No.
TOC
TN
[g × kg d.m.]
Grasslands
BN
BN/TN
TOC
TN
BN/TN
[mg × g d.m.]
[%]
[mg × g d.m.]
[%]
19.08
1.73
42.50
2.46
24.17
2.06
97.41
4.73
2
19.08
2.00
43.99
2.20
26.03
2.88
223.88
7.79
3
17.10
2.00
40.85
2.04
34.42
3.20
128.94
4.03
4
11.62
1.35
37.26
2.77
30.33
2.99
132.56
4.43
5
9.88
1.32
23.94
1.82
19.89
2.43
111.96
4.60
6
6.47
1.15
19.18
1.68
29.02
2.29
121.98
5.32
7
9.82
0.85
25.01
2.94
34.95
2.22
126.65
5.70
Mean*
13.29a
1.49a
33.25a
2.27a
28.40b
2.58b
134.77b
5.23b
–1
[g × kg d.m.]
BN
1
–1
–1
–1
* Means marked in column with the different letters are significant at p < 0.05 according to Tukey test.
The indicator characterizing the soil health state is the share of microbial biomass
nitrogen in total nitrogen content [1, 15]. The values of this indicator (1.68–2.94 % for
plough lands and 4.03–7.79 % for grasslands) allow to regard the studied soils as
microbiologically active and in good health state. The highest value of the discussed
indicator was noted on site 2 for grasslands (7.79 %). High biological activity of soil on
this land might have been affected by annual farmyard manure application. The quota of
microbial biomass nitrogen in its total content was also high in the meadow soil from
Dobrocin (site 7), which was left unfertilized (Table 2). It confirms the reports of other
authors, that farmyard manure fertilization and/or lack of mineral treatment stimulate
soil biological activity [5].
The content of microorganism biomass nitrogen in the analyzed soils was positively
correlated with total nitrogen and organic carbon concentrations, cation exchange
capacity and soil abundance in magnesium (both available and exchangeable forms) and
in exchangeable sodium and negatively with clay content (Table 5). The problem of
dependence of microorganism biomass nitrogen content on organic carbon and total
nitrogen contents are often brought up aspects of soil investigation [2, 3, 15]. Former
investigations [2, 16] also pointed to the dependence of the discussed parameter on pH,
which was not corroborated by the conducted research. It is most frequently assumed
that pH assessed in H2O, which is most advantageous for microorganism activity in soil
is 6.5 [2, 16]. In the investigated soils pH ranged widely between 4.9 and 7.7 (Table 3),
however its effect on microorganism biomass content was not registered. In the soils
with pH values approximate to assessed in the analyzed soils Kara and Bolat [2]
demonstrated its negative correlation with BN, significant at p < 0.01. The same authors
5.6
5.6
5.9
5.5
5.3
7.7
5.1
5.8
2
3
4
5
6
7
Mean
pH in H2O
1
No.
14.3
7
15
10
24
18
15
11
< 0.002 mm
[%]
121.5
158.6
52.8
61.2
11.5
364.6
109.9
91.8
P
286.2
101.2
226.0
269.7
113.7
313.4
482.3
496.9
K
100.9
39.6
70.8
54.9
98.8
96.3
191.7
154.4
Mg
Available components [mg × kg–1]
Arable soils
5.7
4.9
6.4
6.6
5.5
5.3
5.6
5.5
pH in H2O
8.1
5
4
5
14
9
11
9
< 0.002 mm
[%]
Selected properties of surface horizons of analyzed soils
25.8
36.7
25.5
16.7
16.7
48.3
35.8
1.1
P
210.1
169.8
176.1
51.3
188.6
138.6
671.6
74.6
K
167.7
318.3
72.1
114.6
180.4
118.9
260.0
109.8
Mg
Available components [mg × kg–1]
Grasslands
Table 3
581
a
62.7
69.9
76.8
81.0
17.3
105.7
11.3
60.7
1
2
3
4
5
6
7
Mean
5.8
2.0
5.6
2.7
6.9
6.6
10.0
7.0
Mg2+
BC – exchangeable bases;
Ca2+
No
b
K+
BCa
4.6
1.7
3.9
3.5
1.9
5.5
7.8
7.7
71.9
15.6
115.8
24.1
90.3
90.0
89.0
78.6
49.3
60.6
11.4
58.0
56.1
44.3
58.2
56.7
H+
CEC – cation exchange capacity;
0.9
0.6
0.7
0.7
0.5
1.0
1.4
1.2
[mmol(+) × kg–1]
Na+
Arable soils
c
55.5
20.5
91.1
29.4
61.7
67.0
60.5
58.1
[%]
BSc
73.6
38.8
112.3
77.5
92.6
84.6
73.5
35.7
Ca2+
BS – base saturation ratio.
121.2
76.3
127.2
82.1
146.4
134.3
147.2
135.3
CECb
9.4
14.5
4.6
7.5
12.4
8.8
13.1
5.1
Mg2+
K+
BCa
Grasslands
1.2
1.6
0.9
0.7
0.9
1.7
2.0
0.6
3.6
3.3
3.1
0.9
3.4
2.5
10.1
2.0
87.8
58.2
120.8
86.6
109.4
97.6
98.6
43.4
[mmol(+) × kg–1]
Na+
Sorption properties of surface horizons of analyzed soils
57.5
66.3
21.8
30.0
61.9
69.0
65.7
88.1
H+
145.3
124.5
142.6
116.6
171.2
166.7
164.3
131.4
CECb
60.2
46.8
84.7
74.3
63.9
58.6
60.0
33.0
[%]
BSc
Table 4
582
583
obtained, similar as in presented results, a negative relationship between BN and clay
content.
In the analyzed soils the share of microorganism biomass nitrogen in total nitrogen
content depended on its soil concentrations. It was also positively correlated with
magnesium content (Table 5).
Table 5
Values of Spearman rank correlation coefficients
Soil
properties
BN
BN/TN
a
p £ 0.01,
TN
BN/TN
0.914
b
0.681
b
b
0.879
—
b
TOC
0.903
b
0.725
b
pH in
H 2O
–0.047
–0.022
< 0.002
mm
–0.681
a
–0.532
a
P
Mg2+
Mg
available
–0.281
–0.437
Na+
CEC
exchangeable
0.665
a
0.454
a
0.608
a
0.558a
0.588a
0.345
a
a
0.368a
0.273
p £ 0.001.
Conclusions
1. Arable soils of the Silesian and Ciezkowickie Foothills were characterized by a
high share of microorganism biomass nitrogen in its total content, which allows them to
include to soils with a high biological activity and in a good health state.
2. It was ascertained that, the soil management method was a significant factor
affecting the microbial biomass nitrogen content. The contents of microorganism
biomass nitrogen and its share in total nitrogen content in grassland soils were much
higher than in arable soils.
3. The content of microorganism biomass nitrogen in the studied soils was positively
correlated with the contents of total nitrogen and organic carbon, cation exchange
capacity and soil abundance in magnesium (both available and exchangeable forms) and
in exchangeable sodium.
4. The nitrogen content in soils was the factor determining the share of microbial
biomass nitrogen in its total content.
Acknowledgement
The studies were financed by the Ministry of Science and Higher Education, Poland, under the grant No.
N N310 312434.
References
[1] Sparling G.P. [in:] Biological Indicators of Soil Health (eds. Pankhurst C.E., Doube B.M. and Gupta
V.V.S.R.), CAB INTERNATIONAL, 1997, 97–119.
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[3] Chowdhury M.A.H., Kouno K. and Ando T.: Soil Sci. Plant Nutr. 1999, 45(1), 175–186.
[4] Dilly O., Blume H.-P. and Munch J.Ch.: Biogeochemistry 2003, 65(3), 319–339.
[5] Balik J., Èerny J., Tlustoš P., Zitková M., Sýkora K. and Wiœniowska-Kielian B.: Chem. In¿. Ekol. 2004,
11(8), 703–711.
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PN-R-04032: Gleby i utwory mineralne. Pobieranie próbek i oznaczanie sk³adu granulometrycznego,
1998.
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Voroney R.P., Winter J.P. and Beyaert R.P.: Soil microbial biomass C and N, [in:] Carter M.R.: Soil
sampling and methods of analysis. Lewis Publishers, Boca Raton, USA 1993, 277–286.
Chen G. and He Z.: J. Zhejiang Univer. Sci. 2003, 4(4), 480–484.
Acosta-Martinez V. and Tabatabai M.A.: Biol. Fertil. Soils 2000, 31, 85–91.
ZAWARTOŒÆ AZOTU BIOMASY MIKROBIOLOGICZNEJ
W RÓ¯NIE U¯YTKOWANYCH GLEBACH POGÓRZA KARPACKIEGO
Katedra Gleboznawstwa i Ochrony Gleb
Uniwersytet Rolniczy im. Hugona Ko³³¹taja w Krakowie
Abstrakt: W pracy przedstawiono wyniki badañ nad zawartoœci¹ azotu biomasy mikrobiologicznej
w u¿ytkowanych rolniczo glebach Pogórza Œl¹skiego i Ciê¿kowickiego. Wykorzystano materia³ glebowy z 14
profili gleb zlokalizowanych parami – na gruntach ornych i u¿ytkach zielonych s¹siaduj¹cych ze sob¹.
Oznaczono podstawowe w³aœciwoœci gleb oraz zawartoœæ azotu biomasy mikrobiologicznej metod¹ chloroformowej fumigacji-ekstrakcji. Badane gleby charakteryzowa³y siê du¿ym udzia³em azotu biomasy mikroorganizmów w jego ogólnej zawartoœci, co œwiadczy o ich wysokiej aktywnoœci biologicznej. W glebach
u¿ytków zielonych zawartoœæ azotu biomasy mikrobiologicznej i jego udzia³ w ca³kowitej zawartoœci azotu
by³y istotnie wiêksze ni¿ w glebach gruntów ornych. Zawartoœæ azotu biomasy mikroorganizmów by³a
dodatnio skorelowana z zawartoœci¹ azotu ogó³em i wêgla organicznego, pojemnoœci¹ wymienn¹ kationow¹
i zasobnoœci¹ gleb w magnez (przyswajalny i wymienny) oraz sód wymienny.
S³owa kluczowe: Pogórze Œl¹skie i Ciê¿kowickie, sposób u¿ytkowania gleb, azot ogó³em, azot biomasy
mikrobiologicznej
Vol. 18, No. 4
A
2011
Lidia OKTABA1* and Alina KUSIÑSKA1
MINERAL NITROGEN IN SOILS
OF DIFFERENT LAND USE
MINERALNE FORMY AZOTU W GLEBACH
O RÓ¯NYM SPOSOBIE U¯YTKOWANIA
Abstract: Different land use influences both quantity and quality of soil nitrogen, especially its mineral
forms. We conducted our study in Pruszkow soils of four different land using: fields (at the edge of town
border), allotment gardens, lawns and fallows, 36 samples together. The town is part of the Warsaw
agglomeration. It is small but densely populated.
Soil was sampled on July, from 0–20 cm depth. The textures of these soils were sands, loamy sands and
silts.
Amount of total nitrogen in all studied soils was diverse and ranged from 0.33 to 1.91 g × kg–1 dry matter
of soil. The highest average content of this element was found in soils of allotment garden (1.1 g × kg–1 dry
matter of soil), and the lowest one in fallow soils (0.5 g × kg–1 dry matter of soil). Allotment garden soils were
characterized as richest in N-NO3 too (average 22.76 mg × kg–1 dry matter of soil). We observed slightly lower
accumulation of this element in field soils (average 21.52 mg × kg–1 dry matter of soil). In individual cases the
quantity of N-NO3 exceeded even 40 mg × kg–1 dry matter of soil. Significantly lower amount of this element
was found in lawns (average 8.79 mg × kg–1 dry matter of soil) and fallows (average 3.22 mg × kg–1 dry matter
of soil). Different land use had no effect on ammonia amount in Pruszkow soils. The biggest share of N-NO3
in N total was in fields, then in allotment gardens, lawns and smallest in fallows. Share of N-NH4 in N total
decreased in the following order: fields, fallows, lawns, allotment gardens. N-NO3 forms prevailed in fields
and allotment garden, while N-NH4 predominated in lawns and fallows. Soil reaction had no effect on N-NO3
and N-NH4 amount and N–NO3/N-NH4 ratio.
We assumed that actual way of land use affects total nitrogen content and N-NO3 content in soil. In town
environment soils of allotment garden can contribute to water pollution.
Keywords: mineral nitrogen, land use, ammonia, nitrate
Organic compounds are the substantial part of soil nitrogen. Mineral forms account
only for 1–2 % of total nitrogen, but these compounds take part in plant nutrition. If
their amount exceeds the plant needs, they can be leached to water and cause its
pollution. Nitrogen from fertilizers is utilized by plants only in 50–70 % [1]. Ammonia
ions can be absorbed by the soil sorption complex. Nitrate ions are rinsed predominant1
Department of Soil Environment Science, Soil Science Division, Warsaw University of Life Science, ul.
Nowoursynowska 159, 02–776, Warszawa, Poland, phone: +48 22 593 26 10, email: [email protected]
586
Lidia Oktaba and Alina Kusiñska
ly [2]. The attention of scientists is mainly focused on different fertilizers effects,
different doses in various times, under different plants on nitrogen mineralization – its
process and efficiency [3–11]. In natural environment chemical and physical properties
of soil are the main factor controlling nitrogen turnover and mineralization [7, 12].
Our objective was to find how strongly different using of soils in Pruszkow area
affects N mineral and if there exists the risk of water enrichment with N compounds.
Samples of soils were taken in July 2005 from Pruszkow area. This town is part of
the Mazowia province, Pruszkow district, near river Utrata. This is the smallest but
densely populated district in the province. Big concentration of people may cause a
problem to environmental protection of this region. During soil sampling the weather
was sunny and it was very hot (beyond 30 oC) and dry. These situation lasted more than
the month.
We have chosen: arable soil (at the town edge) – 9 samples, soils from allotment
garden – 11 samples, lawns – 12 samples and fallows – 4 samples (36 points together).
Soil was taken from 0–20 cm depth (mixed samples) – surface layer is the most
important part of soil profile in N mineral accumulation, and where turnover of N is
most dynamic [3, 13–15].
Total nitrogen was measured by Kjeldahl method, N-NO3 and N-NH4 after extraction
in 1 % K2SO4 by the colorimetric method using the SAN plus SYSTEM analyzer, pH in
H2O and 1 M KCl – electrometrically, C organic using the TOC 5000A Shimadzu
analyzer. The texture of soils was determined according to Cassagrande’a procedure –
modified by Proszynski [16]. Sum of mineral forms percentage in N total, share of
N-NO3 and N-NH4 in N total and N-NO3/N-NH4 ratio were calculated. Multiple sample
comparisons between soils of different land use were made using Statgraphics Plus 4.1.
software.
According to Pruszkow District Office data [17] soils prevailed on study area were
leached brown soils and typical lessivés soils – by Polish Classification [18] or Dystric
Cambisols and Haplic Luvisols – by WRB [19].
Majority of study soils were sands with small amount of clay particle (< 0.02 mm) or
silts (Table 1).
The amount of total nitrogen in all studied soils varied greatly and ranged from 0.33
to 1.91 g × kg–1 dry matter of soil (Table 2). The biggest average content of this element
was found in soils of allotment garden, 0.63 – 1.91 g × kg–1 dry matter of soil (average
1.11 g × kg–1 dry matter of soil). Average content of total nitrogen in other soils was
considerably lower and it was rather similar among groups and the smallest was in
fallow soils (0.48 g × kg–1 dry matter of soil – Table 3). It is known that stable bulk soil
N pool is positively correlated with soil C content [20]. Usually owners of allotment
garden improve their soils with organic matter such as compost, manure or different
Mineral Nitrogen in Soils of Different Land Use
587
organic waste. Soils enriched with organic matter and lime usually have neutral or close
to neutral soil reaction (pH in allotment garden usually was over 7). This conditions
favour the nitrification process. This is reflected in the quantity of nitrate forms.
Table 1
Soils textures
1–01 mm
Way of
land use
Arable
fields
Lawns
Allotment
gardens
Fallows
Sample
No.
>1 mm
1
2
4
5A
5B
6
8
28
30
15A
15B
15C
16
17
18
29
32
33A
33B
35
36
19A
19B
19C
20A
20B
20C
22A
22B
31A
31B
31C
3
7
9
34
1.36
1.72
7.47
1.12
1.65
1.26
1.41
1.59
1.27
3.37
10.77
3.54
3.24
2.39
2.71
2.55
5.72
12.65
2.89
3.00
1.94
1.38
1.08
1.37
0.63
3.13
5.66
1.66
2.34
3.43
1.11
0.50
1.58
4.20
5.68
2.97
0.1–0.02 mm
< 0.02 mm
1.00–
–0.50
0.50–
–0.25
0.25–
–0.10
0.10–
–0.05
0.05–
–0.02
0.02–
–0.006
0.006–
–0.002
< 0.002
0.39
0.69
1.47
0.62
0.30
0.65
0.71
0.33
0.49
0.85
1.63
0.35
0.55
1.43
0.83
0.39
0.56
0.46
1.08
0.58
0.78
0.66
0.72
0.79
0.31
0.58
0.48
0.61
0.56
0.90
0.45
0.26
0.75
0.83
0.47
0.69
7.32
14.04
14.23
11.03
13.93
12.66
10.93
7.49
10.05
24.59
17.52
10.51
25.12
19.68
20.95
11.04
18.33
8.55
10.72
6.97
11.45
12.37
17.1
9.13
8.48
13.01
12.92
17.5
11.36
11.89
6.92
8.49
12.56
15.15
18.66
21.35
32.29
38.27
60.30
41.36
49.78
42.69
52.36
46.18
49.46
60.56
55.85
52.14
61.32
63.89
53.22
59.58
53.11
57.00
38.20
43.46
40.77
47.97
53.18
49.08
37.21
32.42
30.60
52.90
35.08
33.21
28.63
24.26
46.69
40.03
60.86
56.96
8
34
9
11
11
8
7
12
14
11
11
11
11
6
11
13
12
7
13
9
12
15
14
15
14
13
15
10
13
17
11
11
8
13
6
7
52
0
11
36
25
35
17
34
26
3
10
24
2
6
11
16
12
27
21
18
18
17
11
22
40
22
41
15
40
18
33
30
20
24
14
6
0
9
4
0
0
1
8
0
0
0
4
2
0
3
3
0
4
0
12
12
13
7
4
4
0
10
0
4
0
12
12
17
8
5
0
6
0
4
0
0
0
0
4
0
0
0
0
0
0
0
0
0
0
0
2
4
2
0
0
0
0
8
0
0
0
7
7
4
4
2
0
2
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
2
6
2
0
0
0
0
1
0
0
0
0
1
5
0
0
0
0
588
Table 2
Content of C organic, N total and soil reaction
Way of
land use
Arable
fields
Lawns
Allotment
gardens
Fallows
pH
Corg
[g × kg–1 dry matter
of soil]
Ntot
[g × kg–1 dry matter
of soil]
C/N
6.86
0.43
15.8
9.02
0.49
18.3
6.30
8.95
0.40
22.7
5.64
4.85
7.81
0.48
16.4
5B
6.28
5.51
6.73
0.40
16.9
6
5.61
4.70
9.32
0.53
17.4
8
6.91
6.47
29.23
1.36
21.5
28
7.69
7.16
24.93
0.71
35.0
27.3
Sample
No.
H 2O
1 M KCl
1
5.50
4.80
2
5.48
4.45
4
6.56
5A
30
6.33
5.44
11.88
0.44
15A
6.58
6.23
18.27
0.79
23.1
15B
5.42
4.55
27.56
0.78
35.6
15C
7.05
6.41
20.39
0.76
26.9
16
7.01
6.44
35.17
1.21
29.2
17
7.64
7.29
19.65
0.82
23.9
18
7.91
7.55
24.18
0.71
34.1
29
6.76
6.41
14.46
0.53
27.4
32
4.47
3.68
24.31
0.99
24.6
33A
6.69
6.44
17.89
0.55
32.4
33B
6.80
6.01
13.70
0.61
22.4
35
6.99
6.82
19.71
0.74
26.6
36
6.85
6.52
11.05
1.46
7.6
19A
7.72
7.19
22.25
1.07
20.9
19B
7.42
7.06
20.42
1.01
20.1
19C
6.59
5.92
24.23
1.35
17.9
20A
7.76
7.29
30.73
1.50
20.5
20B
6.96
6.38
22.38
1.15
19.5
20C
6.94
6.40
36.94
1.91
19.3
22A
7.45
7.16
12.46
0.63
19.8
22B
7.49
7.25
17.27
0.80
21.5
31A
7.35
6.92
22.87
1.21
18.8
31B
7.54
7.24
16.12
0.81
19.8
31C
7.15
6.78
12.96
0.75
17.3
3
6.25
5.56
13.34
0.67
20.0
7
6.60
6.15
9.48
0.45
20.9
9
5.18
4.55
10.70
0.47
22.9
34
7.45
7.34
7.94
0.33
24.2
589
Table 3
Multiple sample comparisons
Way of land using
Statistics for
Nmineral
[mg × kg–1]
Statistics for
N-NO3 in Ntot
[%]
Statistics for
N-NO3
[mg × kg–1]
Fallows
12
11
0.40
0.53
0.63
0.33
Maksimum
1.36
1.46
1.91
0.67
Average
0.58
0.83
1.11
0.48
Variance
0.09
0.07
0.14
0.02
Standard deviation
0.31
0.27
0.38
0.14
0.53
0.33
0.34
0.29
Minimum
12.22
10.61
7.67
5.39
Maksimum
59.31
33.78
50.70
19.49
Average
34.66
20.10
32.69
11.41
Variance
403.75
62.76
191.27
31.38
20.09
7.92
13.83
5.60
0.58
0.39
0.42
0.49
Minimum
1.4
1.4
0.7
1.2
Maksimum
4
14.7
6.4
4.4
5.8
Average
7.3
2.6
3.0
2.7
Variance
26.28
2.19
1.17
4.41
Standard deviation
5.13
1.48
1.08
2.10
0.70
0.56
0.36
0.77
Minimum
0.0
0.0
0.2
0.0
Maksimum
10.8
4.0
3.6
3.3
Average
4.6
1.2
2.0
0.9
Variance
18.35
1.41
1.07
2.52
Standard deviation
4.28
1.19
1.03
1.59
0.92
1.02
0.52
1.71
Minimum
0.00
0.00
1.80
0.00
Maksimum
43.30
21.80
43.50
10.70
Average
21.52
8.79
22.76
3.22
Variance
322.29
58.26
197.29
25.16
17.95
7.63
14.05
5.02
0.83
0.87
0.62
1.56
Minimum
6.28
7.76
1.33
5.39
Maksimum
17.60
15.25
13.40
9.70
Average
13.14
11.31
9.94
8.19
Variance
16.32
4.62
12.79
3.90
Standard deviation
4.04
2.15
3.58
1.97
0.31
0.19
0.36
0.24
Standard deviation
Statistics for
N-NH4
[mg × kg–1]
Allotment
gardens
9
Standard deviation
Statistics for
Nmineral in Ntot
[%]
Lawns
Minimum
Count
Statistics for
Ntot [g × kg–1]
Arable
fields
590
Comparing soils of different land use in mineral compound enrichment (N-NO3 +
N-NH4) we can notice that agricultural soils and allotment garden soils are significantly
more abundant than soils of lawns and fallows (average in sequence was: 34.66; 32.69;
20.10 and 11.41 mg × kg–1 dry matter of soil – Table 3). The differences were
statistically significant (p = 0.05). The share of N mineral in N total was the biggest in
fields too. It amounted to over 7 %. It was only 2.6 % to 3.0 % in the rest of soils.
Land use form influenced the domination of N-NO3 or N-NH4 forms. Nitrate
prevailed in samples collected from fields and allotment gardens while ammonia
dominated in fallows and lawns (even in park). N-NH4 is usually a main form in forest
soils [21, 22] and in orchard too [23]. Acid reaction of soil favoured this phenomenon
[21, 22]. We did not prove the influence of soil reaction on N-NO3/N-NH4 ratio.
Share of N-NO3 in N total was the biggest in fields (average 4.6 %), smaller in
allotment garden soils (2.0 %), lawns (1.2 %) and in fallow (0.9 %) – Table 3. Probably,
fertilizing favours big percentage of this form. Bielinska and Domzal [24] claimed that
N-NO3 amounted 1–5 % of N total in top layer in orchard with fertilizers, and only
0.1–0.5 % without fertilizers.
As it was mentioned previously, convenient conditions to nitrification existed in soils
of allotment gardens. It was why allotment garden soils were characterized as most
abundant in N-NO3 (average 22.76 mg × kg–1 dry matter of soil). It was about 68 kg per
hectare in 0–20 cm layer. This amount could not be used by plant and is subject to
leaching to groundwater [25]. Slightly lower accumulation of this element was observed
in field soils (average 21.52 mg × kg–1 dry matter of soil). In individual cases the
quantity of N-NO3 exceeded even 40 mg × kg–1 dry matter of soil. The nitrate quantity in
fields soils was significantly higher than in the others (Table 3). Applied fertilizers
promote intensive nitrification [5, 15, 26].
Turnover of nitrogen lead to acidification of environment [25]. In this study it led to
decrease in field soils pH (Table 2).
Different land use had no affect on ammonia amount in Pruszkow soils. Average
content of N-NH4 was 8.19 – 13.14 mg × kg–1 dry matter of soil. The share of N-NH4 in
N total was in the following order: fields, fallows, lawns, allotment gardens. Fertilizing
had not affected this form’s content. The same result obtained Bielinska and Domzal
[24].
Conclusions
1. Way of land use affected total nitrogen content and N-NO3 content in soil. The
biggest accumulation occured in soils under agricultural use and in allotment garden.
2. Soil reaction did not influence N-NO3 and N-NH4 amount and N–NO3/N-NH4
ratio in studied soils.
3. Different land use had no affect on ammonia amount in Pruszkow soils. This is
rather a stable environmental element.
4. Soils of allotment garden could become source of water pollution in town
environment in the same range as fields.
591
References
[1] Mercik S., £abêtowicz J., Sosulski T. and Stêpieñ W.: Nawozy i Nawo¿enie 2002, 1(10), 228–237.
[2] Sykut S.: Dynamika procesu wymywania azotanów z gleb w doœwiadczeniu lizymetrycznym, [in:] Rola
Gleby w Funkcjonowaniu Ekosystemu, Kongres PTG 1999, streszczenia, 383–384.
[3] Fotyma E., Fotyma M., Pietruch Cz. and Berge H.: Nawozy i Nawo¿enie 2002, 1, 30–49.
[4] Grignani C and Zavattaro L.: Eur. J. Agron. 2000, 12, 251–268.
[5] Nowak L., Kruhlak A., Chyliñska E. and Dmowski Z.: In¿. Roln. 2005, 4(64), 57–66.
[6] Sapek B.: Zesz. Probl. Post. Nauk Rol. 2006, 513, 345–354.
[7] Sapek B. and Kaliñska D.: Woda – Œrodowisko – Obszary Wiejskie 2004, 1(10), 183–200.
[8] Sosulski T. and £abêtowicz J.: Zesz. Probl. Post. Nauk Roln. 2006, 513, 423–432.
[9] Sosulski T., Mercik S. and Stêpieñ W.: Zesz. Probl. Post. Nauk Roln. 2006, 513, 447–455.
[11] Steinberg M., Aronsson H., Lindén B., Rydberg T. and Gustafson A.: Soil Till. Res. 1999, 50, 115–125.
[12] Spychaj-Fabisiak E. and Murawska B.: Zesz. Probl. Post. Nauk Roln. 2006, 513, 465–471.
[13] Paul K., Black S. and Conyers M.: Plant Soil 2001, 234(2), 239–246.
[14] Skowroñska M.: Annales UMCS 2004, 59(2), sec. E, 655–665.
[15] Vestgarden L.S. and Kjønaas O.J.: Forest Ecol. Manage. 2003, 174, 191–202.
[16] Ostrowska A., Gawliñski S. and Szczubia³ka Z.: Metody analizy i oceny w³aœciwoœci gleb i roœlin. Inst.
Ochr. Œrodow., Katalog, Warszawa 1991, 21–38.
[17] Rada i Zarz¹d Powiatu Pruszkowskiego: Strategia rozwoju Powiatu Pruszkowskiego do 2025. Pruszków
2005, 9–10.
[18] Polskie Towarzystwo Gleboznawcze: Systematyka Gleb Polski. Rocz. Glebozn. 1989, 40(3/4), 92–93.
[19] World reference base for soil resources. A framework for international classification, correlation and
communication. World soil resources report 103, Rome 2006.
[20] Kaye J., Barrett J. and Burke I.: Ecosystems 2002, 5, 461–471.
[21] Bro¿ek S.: Rocz. Glebozn. 1985, 36(3), 91–108.
[22] Czêpiñska-Kamiñska D., Rutkowski A. and Zakrzewski S.: Rocz. Glebozn. 1999, 50(4), 47–56.
[23] Kozanecka T.: Rocz. Glebozn. 1995, 46(1/2), 105–117.
[24] Bieliñska E.J. and Dom¿a³ H.: Rocz. Glebozn. 1998, 49(3/4), 31–39.
[25] Sapek B.: Wymywanie azotanów oraz zakwaszenie gleby i wód gruntowych w aspekcie dzia³alnoœci
rolniczej. Wyd. IMUZ 1995.
[26] Sapek A. and Sapek B.: Zesz. Probl. Post. Nauk Roln. 2006, 513, 355–364.
MINERALNE FORMY AZOTU W GLEBACH O RÓ¯NYM SPOSOBIE U¯YTKOWANIA
Katedra Nauk o Œrodowisku Glebowym
Szko³a G³ówna Gospodarstwa Wiejskiego w Warszawie
Abstrakt: Sposób u¿ytkowania wp³ywa na iloœæ i jakoœæ zwi¹zków azotu, w szczególnoœci po³¹czeñ
mineralnych. Badano gleby Pruszkowa bêd¹ce w u¿ytkowaniu: rolniczym (na obrze¿ach miasta), gleby
ogródków dzia³kowych, gleby trawników w parkach i zieleñców przyulicznych oraz nieu¿ytków (³¹cznie 36
próbek z terenu ca³ego miasta). Miasto to jest czêœci¹ aglomeracji warszawskiej i charakteryzuje siê du¿ym
zaludnieniem.
Glebê pobierano w lipcu, z g³êbokoœci 0–20 cm. By³y to g³ównie piaski, piaski pylaste (od luŸnych do
gliniastych) i py³y zwyk³e.
Iloœæ azotu ogó³em w badanych glebach znajdowa³a siê w granicach 0,33–1,91 g × kg–1 s.m. gleby.
Najwiêksz¹ œredni¹ zawartoœci¹ tego pierwiastka charakteryzowa³y siê gleby ogródków dzia³kowych (1,1
g × kg–1 s.m. gleby), a najmniejsz¹ gleby nieu¿ytków (0,5 g × kg–1 s.m. gleby). Gleby ogródków dzia³kowych
zawiera³y równie¿ œrednio najwiêksze iloœci azotu azotanowego (22,76 mg N-NO3 × kg–1 s.m. gleby).
Nieznacznie mniejsz¹ iloœæ tej formy stwierdzono w glebach pól (œrednio 21,52 mg N-NO3 × kg–1 s.m. gleby).
W pojedynczych przypadkach iloœci te by³y znacznie wiêksze i przekracza³y 40 mg N-NO3 × kg–1 s.m. gleby.
Istotnie ni¿sz¹ iloœæ tej formy stwierdzono w glebach trawników (œrednio 8,79 mg N-NO3 × kg–1 s.m. gleby)
i nieu¿ytków (œrednio 3,22 mg N-NO3 × kg–1 s.m. gleby).
592
W przypadku azotu amonowego nie wykazano wp³ywu ró¿nego u¿ytkowania na zawartoœæ tej formy
w glebie. Udzia³ azotu azotanowego w ogólnej iloœci azotu najwiêkszy by³ w glebach pól uprawnych,
nastêpnie ogródków dzia³kowych, trawników i najmniejszy w glebach nieu¿ytków. Udzia³ N-NH4 w N
ogó³em wystêpowa³ kolejno w glebach: pól, nieu¿ytków, trawników, ogródków dzia³kowych. W glebach pól
i ogródków dzia³kowych przewa¿a³a forma azotanowa, natomiast forma amonowa przewa¿a³a w glebach
trawników i nieu¿ytków. Nie stwierdzono wp³ywu odczynu gleby na iloœæ form N-NO3 i N-NH4 oraz na
wartoœæ stosunku N-NO3 /N-NH4.
Na podstawie przeprowadzonych badañ i analiz mo¿emy stwierdziæ, ¿e sposób u¿ytkowania gleby na
terenie Pruszkowa wywiera istotny wp³yw na zawartoœæ azotu ogó³em i azotanów w glebie. Gleby ogródków
dzia³kowych mog¹ byæ potencjalnym Ÿród³em zanieczyszczenia wód tym elementem.
S³owa kluczowe: azot mineralny, sposób u¿ytkowania terenu
A
Vol. 18, No. 4
2011
Joanna ONUCH-AMBORSKA1
EFFECT OF DIFFERENT DOSES OF NITROGEN
ON SOIL QUALITY AND YIELD OF PLANTS
GROWN IN THE LAND RECULTIVATED
AFTER SULPHUR MINING
WP£YW ZRÓ¯NICOWANYCH DAWEK AZOTU NA GLEBÊ
ORAZ JAKOŒÆ ROŒLIN UPRAWIANYCH
NA REKULTYWOWANYCH TERENACH GÓRNICZYCH
Abstract: The aim of this work was to determine the effect of different doses of nitrogen fertilizers on soil
properties and the yielding of plants and the usable value of the grass in the sulphur mining activity area
where the recultivation efforts were carried out. It was found that sowing a mixture of grassland plants and the
application of nitrogen fertilization in the recultivated area significantly improves the properties of the soil
environment. The increasing doses of nitrogen contributed to the vigorous growth of plants, which resulted in
a sulphur content reduction, changes of the reaction and a significant increase in the content of organic matter
in the soil. The results showed that the mineral nitrogen fertilization favorably affects the yield of plants as
well as the quality of the obtained grass.
Keywords: nitrogen fertilization, recultivated land, plant yield
Mine sulphur activity causes adverse changes in the natural environment. It results in
the devastation of soils, the landscape components changes and hydrological and
geomechanical transformations of the site, excluding the land from agricultural or forest
production [1–3]. Rehabilitation of such sites should aim at restoration of the natural
and the usable values of the environment. The last stage in the process of rehabilitation
is the introduction of grasslands or forests [4, 5]. The mineral and organic fertilization is
needed to provide the plants introduced to the recultivated areas with the adequate
quantities of necessary nutrients for growth and development. [6]. One of the most
important yield- generating elements is nitrogen. It substantially determines the fertility
level of soils and obtained yields [7]. However, an excessive mineral fertilization can
significantly deteriorate the quality of grasses [8].
1
Faculty of Agricultural Sciences, University of Life Science in Lublin, ul. Szczebrzeska 102, 22–400
Zamoœæ, Poland, phone: +48 84 627 27 42, email: [email protected]
594
Joanna Onuch-Amborska
This paper presents the results of research aimed at identifying the impact of different
doses of nitrogen fertilizers on the soil properties, yielding of plants and usable values
of the grass in the area of sulphuric mining activities, where the recultivation efforts
were carried out.
The research was conducted in the former sulphur mine ‘Jeziórko’ near Tarnobrzeg
in Podkarpackie province, which was subjected to rehabilitation treatment. The
recultivation included the neutralization, blockade and isolation of contamination,
regulation of water conditions, cleaning of the terrain, mineral and organic fertilization
and the introduction of vegetation. The last step in the biological rehabilitation was
sowing of a grass and Fabaceae mixture and a supplementary fertilization.
The experiment was founded on a separate area, which had been prepared for the
final phase of the recultivation. The experiment with 4 different doses of nitrogen
fertilizers – 80 kg N × ha–1, 160 kg N × ha–1, 240 kg N × ha–1, 320 kg N × ha–1, each with 3
replications, was set up on the prepared fields covering a surface of 100 m2. These
fertilizers were sown in 3 doses: 50 % before sowing a mixture of grasses, 30 % after
the first swath, 20 % after the second swath. The check plots were not fertilized.
In May of 2000 the fields were sown with a prepared grass mixture of 60 kg × ha–1,
which included: Meadow fescue Festuca pratensis 58 %, Red fescue Festuca rubra
15 %, Italian ryegrass Lolium multiflorum 14 %, Red clover Trifolium pratense 8 % and
Cocksfoot Dactylis glomerata 5 %.
Before sowing the mixture of grass, the soil samples (0–20 cm level) for the
laboratory analysis had been collected from each plot. These samples were dried, sifted
through a sieve with a mesh with 1 mm openings. Then, the following indications were
made: the granulometric composition due to Cassagrande method with the Proszynski
modification, the soil reaction (potentiometrically in H2Odist. and 1 M KCl), the organic
matter quantity (Tiurin method) and the sulphur content (nefelometric method). The soil
properties study was also carried out in autumn of 2000 and spring and autumn of 2001,
while cropping of the plants (spring and autumn swath).
To determine the effect of nitrogen fertilization on the yielding of plants and the
value of agricultural grass in the autumn of 2000 and in spring and autumn of 2001 the
vegetation test samples were collected from the surface of 1 m2. Based on the
botanical-gravimetric analyses according to Filipek [9] the number of usable value of
grass (LWU) was calculated. The obtained data was analyzed with a Tukey statistical
test.
The results of soil tests carried out before the foundation of the experience revealed
considerable variation in the properties of the soil environment. The plots was
established on soils granulometrically composed of loose sand. Soil reaction ranged
Effect of Different Doses of Nitrogen on Soil Quality and Yield of Plants...
595
from very strongly acid to slightly acid (Table 1). The lowest reported reaction was in
the plot number 3, where the highest sulphur content was found.
Table 1
The proprieties of soil environment before installed experience 1 – plot without fertilization,
2 – 80 kg N × ha–1, 3 – 160 kg N × ha–1, 4 – 240 kg N × ha–1, 5 – 320 kg N × ha–1
pH
S-sulphate
[mg × kg–1]
H2 O
KCl
Organic matter
[%]
S-total
[mg × kg–1]
1
6.5
6.1
3.07
192
89
2
4.9
4.4
3.26
406
322
3
4.5
4.1
3.34
797
645
4
5.6
5.3
3.36
267
145
5
6.3
6.0
3.24
187
53
Plot
Very wide variations in the sulphur content (the total sulphur and sulphate) were
found in the tested area. The studied soils contained from 187 mg × kg–1 (plot no. 5) to
do 797 mg × kg–1 of total sulphur. The sulphur content found in the investigation area
exceeds the average quantity of this element in Polish soils. Motowicka-Terelak and
Terelak [10] report that the amount of total sulphur in Polish sandy soils ranges between
100 and 270 mg × kg–1, and the amount of sulphate ranges between 16 and 169
mg × kg–1. The test plots were also characterized by the slight diversity of organic matter
– from 1.78 % to 1.95 %.
The differences in the properties of the soil environment were observed after sowing
the mixture of grass and after the application of nitrogen fertilizers. The intensive
development of plants in the first year of experience affected the soil reaction. A slight
increase in the pH value was observed in almost all of the plots. The only one with
reduced pH values was the plot number 3 – the one with the highest sulphur content.
The growth of the mixture of grasses and papilionaceous plants contributed to the
increase of organic matter content in soil. The largest increase in humus in relation to its
quantity before the foundation of experience (about 20 %), was registered in the plots
where the nitrogen was applied in a dose of 240 kg × ha–1. In the plots with the highest
dose of nitrogen fertilization the increase in the amount of organic matter was about
17 % smaller (Tables 1, 2).
Sulphur is one of the fundamental macroelements necessary for the proper development of plants. Plants absorb this element from the soil mainly in the form of SO42– [10,
11]. Therefore, the development of plants in the first year of the experience contributed
to the reduction of the amount of sulphur in the soil, both in the total form and as
sulphate. The total sulphur content in the soil in the tested fields decreased proportionally with the increasing doses of nitrogen fertilizers (Fig. 1a). In the plot number 4,
which got a nitric fertilizer in a dose of 240 kg × ha–1 the total amount of sulphur
decreased by 17 %. In the plot number 5, where the quantity of sulphur was the lowest
and the applied dose of nitrogen the highest, the total sulphur content decreased by
27 %. In the plot, that did not get any nitrogen fertilization the total sulphur content
596
Table 2
The proprieties of soil environment and crop of plants characteristic 1 – plot without fertilization,
2 – 80 kg N × ha–1, 3 – 160 kg N × ha–1, 4 – 240 kg N × ha–1, 5 – 320 kg N × ha–1
pH
Plot
H2O
KCl
Organic matter
[%]
Crop of plants
[Mg × ha–1]
Number of usable
value of plants
LWU
IX 2000
1
6.6
6.3
3.64
3.24
9.77
2
5.2
4.4
3.78
3.26
8.98
3
4.8
3.8
3.91
3.42
9.63
4
5.9
5.5
4.05
3.35
9.87
5
6.1
6.0
3.81
2.79
9.83
Mean
5.7
5.2
3.84
3.21
9.62
LSD0.05
0.30
0.22
0.20
—
1.02
V 2001
1
6.6
6.4
3.91
3.89
9.61
2
5.3
4.6
3.86
6.22
9.55
3
4.6
3.9
3.95
5.18
9.42
4
5.7
5.3
4.21
4.14
9.69
5
5.9
5.7
4.05
4.92
9.56
Mean
5.6
5.2
4.00
4.87
9.57
LSD0.05
0.37
0.47
0.15
1.55
0.25
IX 2001
1
6.6
6.3
4.00
2.84
9.62
2
5.3
4.7
3.90
4.99
9.01
3
4.9
4.4
4.00
4.11
9.12
4
5.8
5.6
4.29
3.38
9.14
5
6.0
5.9
4.47
4.97
9.18
Mean
5.7
5.3
4.13
4.06
9.21
LSD0.05
0.34
0.43
0.38
—
—
decreased only by 4 %. The amount of sulphur in the form of sulphate in the soil during
the first year of experience altered more. The biggest changes in the content of sulphate
was found in the plots with the lowest and the highest dose of nitrogen. The smallest
change in the amount of sulphate in the soil was recorded in the plot number 3 and in
the check plot (Fig. 1b).
b)
800
V 2000
IX 2000
V 2001
IX 2001
700
Stot [mg/kg]
600
500
400
300
700
V 2000
IX 2000
V 2001
IX 2001
600
Ssulphate [mg/kg]
a)
597
500
400
300
200
200
100
100
0
0
1
2
3
4
5
1
2
3
4
5
Fig. 1. Change of total sulphur and sulphate sulphur content in soil of plot with nitrogen fertilization (1 – 0
kg N × ha–1, 2 – 80 kg N × ha–1, 3 – 160 kg N × ha–1, 4 – 240 kg N × ha–1, 5 – 320 kg N × ha–1)
The highest yield of hay in the first year of experience was obtained by applying
nitrogen fertilizer at a dose of N-160 kg × ha–1 (Table 2). The yield of plants obtained in
this combination was 3.42 Mg × ha–1. The smallest yield of the dry weight was found
where the highest dose of nitrogen (320 kg × ha–1) was applied. In terms of agricultural
usefulness the meadow grass was valued as very good in the first year of vegetation.
The highest number of utility value of the grass was found in the plot where the
nitrogen was applied in a dose of 240 kg × ha–1, where the LWU was 9.87.
The analysis of soil in the spring of the second year of experience showed a little
change of the reaction. A considerably decrease in pH was found in the plots with the
highest doses of nitrogen (Table 2). The studies of Wasilewski [12] confirm such
a dependence. He found that higher nitrogen fertilization results in significantly lower
pH values in the long- term pastures.
Further development of plants caused a reduction in the average sulphur content in
the tested soils. There was more than a double increase in the sulphate content in the
plot number 5 which is undoubtedly a result of the considerable variation in the soil
environment in the rehabilitated sulphur mining areas.
In the soil of all of the plots, there was a increase in the amount of organic matter. As
confirmed by a statistical analysis, higher doses of nitrogen fertilizers (240 kg × ha–1 and
320 kg × ha–1) considerably influenced the content of organic matter in soil (appropriately by 4 % and 6 %).
The sulphur content in the soil in the spring of the second year of experience was
significantly diversified. The average quantity of total sulphur and sulphur in the
sulphate form in the soil decreased. The only plot with the same total sulphur content as
it had been before the foundation of experience was the plot with the dose of nitrogen of
240 kg × ha–1. It is explained by a very strong transformation of the soil environment, the
rehabilitation and the easy movement of sulphur in the studied area.
The yield of hay in the spring of 2001 increased twice in comparison with the
previous autumn crop. The highest average yield, which was 6.22 Mg × ha–1 was
obtained from the plots with the lowest (80 kg × ha–1) dose of nitrogen. The
combinations with the highest doses of nitrogen gave considerably lower crop of hay. In
598
the plot where nitrogen was applied 240 kg × ha–1 the yield of hay was lower by 34 % in
comparison, in the plot with highest doses of nitrogen the yield decreased by 21 %. The
smallest hay yield – 3.89 Mg × ha–1 was obtained from the plots without nitrogen
fertilizer application. Obtained test results allow to value the grass as a very good. The
highest number of utility value of the grass – 9.69 was obtained using nitrogen in a dose
of 240 kg × ha–1. These results confirm the results of several studies [8, 13, 14], which
found that the mineral fertilizers, especially nitrogen, contributes positively to improvement of the quality of grass. The number of utility value of grass with the nitrogen in
a dose of 80 kg × ha–1 and 160 kg × ha–1 showed significant statistical differences.
The study of soils in autumn in the second year of experience showed the increase of
the reaction only in the plot with the nitrogen fertilizer in a dose of 240 kg × ha–1
(Table 2). The increase in organic matter content in soils of all examined fields in
relation to the amount before the foundation of experience was found. In the plot
number 5, where the nitrogen fertilizer was applied in a dose of 320 kg × ha–1 the
organic matter content in soil increased by 14 % and in the plot number 4 it increased
by 12 %.
The growth of plants contributed to a sulphur content reduction in the studied soils
(Table 2). The average content of total sulphur in the soil decreased by 27 % and
sulphate form of sulphur by 48 % compared with the quantity before the foundation of
experience. The largest amount of sulphur (total and sulphate) was absorbed by the
plants in the plot with the nitrogen fertilizer in a dose of 80 kg × ha–1. The sulphate form
of sulphur is the primary source of sulphuric acid in the soil, and at the same time it is a
source of sulphur which is necessary for plants and microbes. It is important to note that
even a small proportion of sulphates in the soil meets the needs of plant and animal
organisms [10]. The lowest amount of sulphur was absorbed by the plants in the plot
with higher dose of nitrogen (160 kg × ha–1 and 240 kg × ha–1).
Dry matter yields from autumn 2001 swath were lower compared with yields from
the spring one. At the same time, these yields were higher than the yields obtained in
the first year of experience. The highest yield of 4.99 Mg × ha–1 was obtained with the
application of the lowest dose of nitrogen. Higher doses of nitrogen reduced the yield
from the autumn swath. Krzywy [1] showed similar results of nitrogen fertilization in
the experience with Cocksfoot. He adopted the optimum nitrogen fertilization in the
dose of 180 kg × ha–1. In terms of agricultural usefulness the meadow grass was
estimated, as in the other periods of research, as very good.
Conclusions
Areas anthropogenically transformed under the influence of sulphur mining activities
have very variable characteristics of the soil environment, making it difficult to
determine the doses of nitrogen fertilization in the final stage of plants rehabilitation.
The nitrogen fertilization positively influenced the properties of soil environment in
the recultivated area. The increasing dose of nitrogen contributed to the vigorous growth
of plants, which resulted in a reduction in the sulphur content in the soil, changes of the
soil reaction and a significant increase in the content of organic matter in soil.
599
The mix of grasses introduced into the rehabilitated area positively responded to the
nitrogen fertilization, which positively affected the yield of plants obtained. The highest
yield of grass (6.22 Mg × ha–1) was obtained in the second year after the introduction of
plants, with the nitrogen application in a dose of 80 kg × ha–1.
The nitrogen fertilization of the mix of grasses positively affected the quality of
yield. The highest utility value was obtained in autumn swath in the first year of
experience with the fertilization with nitrogen in a dose of 240 kg × ha–1.
References
[1]
[2]
[3]
[4]
[5]
[6]
[7]
[8]
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Rz¹sa S., Mocek A. and Owczarzak W.: Rocz. AR Poznañ 2000, (317), 225–239.
Siuta J.: Mat. Konf. Ochrona i rekultywacja gruntów, Baranów Sandomierski 2000, 158–183.
Bender J. and Gilewska M.: Mat. Konf. Las – Drewno – Ekologia, Poznañ 1995, 7–15.
Krzaklewski W.: Analiza dzia³alnoœci rekultywacyjnej na terenach pogórniczych w g³ównych ga³êziach
przemys³u wydobywczego w Polsce. Wyd. SGGW, Warszawa 1990.
Jankowski K., Ciepiela G.A., Jode³ka J. and Kolczarek R.: Fol. Univ. Agric. Stetin. 197, Agric. 1999, 75,
141–146.
Gooding M.J. and Smith G.P.: Short Communications Fifth ESA Congres. 1998, 229–230.
Bary³a R.: Ann. UMCS, E 1998, 16(53), 139–145.
Filipek J.: Post. Nauk Roln. 1973, (4), 59–68.
Motowicka-Terelak T. and Terelak H.: Fol. Univ. Agric. Stetin., Agric. 2000, 81, 7–17.
Haneklaus S., Bloem E. and Schung E.: Fol. Univ. Agric. Stetin., Agric. 2000, 81, 17–32.
Wasilewski Z.: Zesz. Probl. Post. Nauk Roln. 2003, 493, 719–726.
Mocek A., Rz¹sa S. and Owczarzak W.: Zesz. Probl. Post. Nauk Roln. 1998, 460, 639–651.
Nieszczyporuk A. and Jankowska-Huflejt H.: Zesz. Probl. Post. Nauk Roln. 1999, 465, 657–667.
WP£YW ZRÓ¯NICOWANYCH DAWEK AZOTU NA GLEBÊ ORAZ JAKOŒÆ ROŒLIN
UPRAWIANYCH NA REKULTYWOWANYCH TERENACH GÓRNICZYCH
Wydzia³ Nauk Rolniczych
Uniwersytet Przyrodniczy w Lublinie
Abstrakt: Celem pracy by³o okreœlenie wp³ywu zró¿nicowanych dawek nawozów azotowych na w³aœciwoœci
gleby oraz na plonowanie roœlin i wartoœæ u¿ytkow¹ runi na obszarze dzia³alnoœci górnictwa siarkowego, na
którym przeprowadzono zabiegi rekultywacji. Stwierdzono, i¿ wysiew mieszanki roœlin trawiastych oraz
zastosowanie nawo¿enia azotowego na rekultywowanym obszarze znacznie poprawia w³aœciwoœci œrodowiska glebowego. Wzrastaj¹ce dawki azotu przyczyni³y siê do intensywnego rozwoju roœlin, co spowodowa³o
zmniejszenie zawartoœci siarki, zmiany odczynu oraz znaczny wzrost zawartoœci substancji organicznej
w glebie. Uzyskane wyniki wykaza³y, ¿e mineralne nawo¿enie azotowe wp³ywa dodatnio na iloœæ plonu roœlin
a tak¿e na jakoœæ uzyskanej runi.
S³owa kluczowe: nawo¿enie azotem, tereny rekultywowane, plon roœlin
A
Vol. 18, No. 4
2011
Tomasz SOSULSKI1 and Marian KORC1
EFFECTS OF DIFFERENT MINERAL
AND ORGANIC FERTILIZATION ON THE CONTENT
OF NITROGEN AND CARBON
IN SOIL ORGANIC MATTER FRACTIONS
WP£YW ZRÓ¯NICOWANEGO NAWO¯ENIA MINERALNEGO
I ORGANICZNEGO NA ZAWARTOŒÆ AZOTU I WÊGLA
WE FRAKCJACH MATERII ORGANICZNEJ GLEBY
Abstract: Studies on carbon and nitrogen content in the selected fractions of the soil organic matter were
carried out on the basis of a soil sample collected in 2005 at the experimental field of Department of
Chemistry, Warsaw University of Life Sciences in Lyczyn near Warsaw. After 10 crop-rotations manure
fertilization resulted in an increase in the content of organic carbon and total nitrogen in soil on all objects
treated with this fertilizer. Exclusive mineral fertilization led to an increase in the content of both organic
carbon and total nitrogen in soil on the majority of objects. This increase was lower than that caused by the
manure fertilization. The manure treatment caused an increase in the content in soil of carbon of the studied
organic matter fractions. The share of carbon of individual organic matter fractions remained similar on the
objects treated and not treated with manure. Among the studied nutrients applied in the form of mineral
fertilizers, only nitrogen increased the content of organic carbon, total nitrogen and its fractions in soil
independent of other factors, as treatment with manure or liming. The effects of mineral fertilizers on the
content of organic carbon and soil nitrogen and its fractions in soil were diverse. The humin-acids-carbon to
fulvic-acids-carbon ratio indicated that the amount of fulvic acids generated in the soil had exceeded that of
humic acids. In sandy-loam soils, which have not been treated with organic fertilization for years, there is a
growing deficit of nitrogen used by crops to build the yield. This is confirmed by the very high C:N ratio
found in the soil applied only mineral fertilizers, which amounted to 14:1, whereas the one observed in the
manure fertilized soil equaled to 11.7:1. The vast majority of soil nitrogen is included in humin and fulvic
acids, which are the most dynamic and susceptible to mineralization.
Keywords: long-term experiment, fertilization, soil organic matter, soil carbon, soil nitrogen
The effect of mineral and organic fertilization on organic carbon and total nitrogen in
soil is well described in domestic and foreign literature [1–4]. Many authors indicate
that the increase in content of organic matter and nitrogen in soil is possible by
1
Department of Soil Environments Sciences, Warsaw University of Life Sciences, Nowoursynowska 159,
02–686 Warszawa, Poland, phone: +48 22 593 26 30, email: [email protected]
602
Tomasz Sosulski and Marian Korc
multimanure fertilization [4, 5]. The impact of multimineral fertilization on organic
carbon and total nitrogen in soil is highly variable. Depending on soil, climatic and
agronomic conditions a slight increase or decrease in the content of organic carbon and
total nitrogen in the soil was obtained [4, 6–8]. In contrast, omission of fertilization
reduces the content of these elements in soil. In studies on diagenesis of the organic
matter in different soil types the importance is given to both, the quantitative, and
qualitative changes in the carbon and nitrogen soil content [9, 10]. Fertilization, which
impacts not only the intensity of transformation of organic matter in soil, but also its
chemical properties (eg pH, the contents of components) and physical ones (eg water
capacity), may also affect the humus composition. The aim of this work was to
determine the effect of mineral, mineral-organic and organic fertilization on the carbon
and nitrogen content in selected soil organic matter fractions.
Studies on carbon and nitrogen content in selected fractions of the soil organic matter
were carried out on the basis of a soil sample collected in 2005 at the experimental field
of Department of Agricultural Chemistry, Warsaw University of Life Sciences in
Lyczyn near Warszawa. A long-term experiment, on which the studies were carried out,
was set up in 1960. The following fertilization objects (4 replications) were distributed
randomly within two blocks, with and without manure: control, with individual
components (N, P, K), with two constituents (NP, NK, PK), and with full dose NPK
fertilizer; each object in two versions: with and without liming. Plants were grown in
the following rotation pattern: potatoes, barley, oilseed rape, rye. On the manure-fertilized objects manure was applied at the dose of 37.5 Mg × ha–1 (25 Mg × ha–1 before
the potatoes and 12.5 Mg × ha–1 before rape) in per a crop-rotation. Soil samples were
collected after harvesting of rye, which completed the tenth crop-rotation. The Lyczyn
soil with texture of a sandy loam belongs to the haplic luvisol type with the silt and clay
content of 11 % and 22 % in the Ap and Bt soil layers, respectively. The following
parameters were measured using the Tiurin method: the content of organic carbon in
soil, the alkaline extract (0.1 M NaOH 0.1 M Na4P2O7 · 10 H2O) carbon soil content,
and the humin acids carbon soil content, the latter following precipitation of humin
acids with sulfuric acid. The fulvic acids carbon soil content was calculated as the
difference between the alkaline extract carbon soil content and the humin acids carbon
soil content. The content of the following parameters was measured using a modified
Kiejdahl method: the total nitrogen soil content, the alkaline extract nitrogen soil
content, and the humin acids nitrogen soil content. The fulvic acids nitrogen soil content
was calculated as the difference between the alkaline extract nitrogen soil content and
the humin acids nitrogen soil content. Additionally, carbon and nitrogen contained in
the post-alkaline-extraction fraction were calculated respectively as the difference
between the content of organic carbon in soil and the alkaline extract carbon soil
content, and the difference between the total nitrogen soil content and the alkaline
extract nitrogen soil content.
Effects of Different Mineral and Organic Fertilization...
603
The paper presents average values of the measured parameters, which characterize
the main effects of the studied nutrients applied in the form of mineral fertilizers
(nitrogen, phosphorus, potassium and liming) and manure. In order to characterize the
main effects of the studied nutrients applied in the form of mineral fertilizers (nitrogen,
phosphorus, potassium and liming) and manure, the studied parameters are depicted in
this paper as values averaged of the results obtained on the objects fertilized with the
nutrients in question.
Influence of fertilization on the content of organic carbon
and its fractions in soil
The baseline content of organic carbon in soil, before the experiment set-up in 1960,
was 5.8 g C · kg–1 [11]. After 10 crop-rotations manure fertilization resulted in an
increase in the content of organic carbon in soil on all objects treated with this fertilizer.
Exclusive mineral fertilization led to an increase in the content of organic carbon in soil
on the majority of objects. This increase, however, was significantly lower than that
caused by the manure fertilization. The content of organic carbon in soil was decreased
versus the baseline only on the objects, which had not been treated with nitrogen and
potassium (Table 1).
From among the studied factors, the manure fertilization was shown to have the
biggest influence on the content of organic carbon in soil and the content in soil of
carbon of individual organic matter fractions (Table 1).
Regardless of the fact that the manure treatment caused an increase in the content of
carbon of the studied organic matter fractions in soil, the share of carbon of individual
organic matter fractions remained similar on the objects treated and not treated with
manure. It can be concluded that manure affects the nature and specific properties of the
soil organic matter only to a limited extent, whereas it is essential to its quantitative
development. The effects of mineral fertilizers on the content of organic carbon and its
fractions in soil were diverse. As expected, the lowest content of organic carbon and its
fractions in soil was found on the objects, which had not been treated with nitrogen
fertilizers nor manure. Among the studied nutrients applied in the form of mineral
fertilizers, only nitrogen increased the content of organic carbon and its fractions in soil
independent of other factors, as treatment with manure or liming. The influence of other
nutrients (phosphorus and potassium) and liming on organic carbon content and its
fractions in soil was lower than the effect of nitrogen, and dependent on the manure
fertilization. On the non-manure-treated objects the use of potassium led to a 15 %
increase in the content of organic carbon in soil. However, application of potassium
fertilization and liming to manure-fertilized objects did not result in major differences in
the content of organic carbon in soil. Neither liming nor fertilization with phosphorus
influenced the content of organic carbon in soil on the non-manure-treated objects. To
note, the content of organic carbon in soil found on these objects was lower than on the
objects treated with potassium. On the other hand, the application of phosphorus to the
With
manure
Without
manure
—
mean
5.3
with P
5.6
5.4
without P
5.0
5.3
with N
with lime
5.4
without N
without lime
—
mean
5.3
5.5
with lime
with K
4.7
without lime
5.3
5.2
without K
5.0
with P
with K
5.3
without P
without K
4.9
4.9
with N
5.3
pHKCl
without N
Treatments
9.265
9.292
9.238
9.142
9.388
8.788
9.742
9.892
8.638
6.225
6.240
6.209
6.653
5.796
6.216
6.233
6.800
5.649
[g · kg–1]
Corg.
38.5
38.3
38.6
37.9
39.0
38.3
38.6
40.5
36.5
38.8
42.2
35.4
37.8
39.7
37.3
40.2
42.2
35.4
[% in Corg.]
3.555
3.544
3.565
3.469
3.640
3.346
3.764
3.978
3.132
2.401
2.584
2.219
2.493
2.310
2.297
2.506
2.868
1.934
[g · kg–1]
Alkaline extract. carbon
17.1
17.3
16.9
15.7
18.5
17.3
16.9
16.3
17.9
18.3
21.5
15.2
15.7
20.9
17.9
18.7
19.3
17.3
[% in Corg.]
1.573
1.597
1.549
1.438
1.707
1.504
1.642
1.604
1.542
1.119
1.309
0.930
1.042
1.196
1.103
1.136
1.302
0.936
[g · kg–1]
Humin acids carbon
(CH)
21.4
21.1
21.7
22.2
20.5
21.1
21.7
24.2
18.6
20.5
20.7
20.2
22.1
18.8
19.4
21.5
22.8
18.1
[% in Corg.]
1.982
1.947
2.016
2.030
1.933
1.842
2.122
2.373
1.590
1.282
1.275
1.289
1.451
1.114
1.195
1.370
1.566
0.998
[g · kg–1]
Fulvic acids carbon
(CF)
Soil pH and the content of organic carbon and its fraction in soil.
0.8:1
0.8:1
0.8:1
0.7:1
0.9:1
0.8:1
0.8:1
0.7:1
1.0:1
0.9:1
1.0:1
0.7:1
0.7:1
1.1:1
0.9:1
0.8:1
0.8:1
0.9:1
CH/CF
61.1
61.7
61.4
62.1
61.0
61.7
61.4
59.6
63.6
61.2
57.8
64.6
62.2
60.3
62.7
59.8
57.8
64.6
[% in Corg.]
5.710
5.748
5.673
5.673
5.748
5.442
5.978
5.914
5.506
3.823
3.656
3.990
4.160
3.486
3.919
3.727
3.932
3.715
[g · kg–1]
Extraction residue
carbon
Table 1
604
605
manured objects led to a 10 % decrease in the content of organic carbon in soil. The
lowest content of humin acid carbon in soil was found on the objects, which had not
been treated with nitrogen fertilizers and in those, which had not been limed. The use of
nitrogen fertilizers and liming resulted in a similar increase in the humin acids carbon
content in soil. These relationships were independent of manure fertilization. The
application of nitrogen fertilizers and liming to the non-manure-treated objects resulted
in an increase in the share of humin acid carbon in the soil organic carbon. No such
relationship was shown on the manured objects. The omission of phosphoric and
potassium fertilization resulted in an increase in the soil humin acid carbon as compared
with the objects, where these fertilizers had been applied. In most instances it caused an
increase in the share of humin acid carbon in the soil organic carbon. The humin-acids-carbon to fulvic-acids-carbon ratio indicated that the amount of fulvic acids
generated in the soil had exceeded that of humic acids. Similar quantities of humin and
fulvic acids were generated solely on the manure-treated objects, which had been limed
and those that had not been treated with potassium, and on non-manure-treated objects,
which had not been treated with nitrogen. Opposite results were obtained by Kusinska
on a sandy loam soil in the Skierniewice experiment [12]. Regardless of the use of
manure, both nitrogen and potassium treatments increased the content of fulvic acid
carbon in soil, whereas liming and phosphorus treatment decreased this parameter. In
most instances, the application of nitrogen, phosphorus and potassium fertilizers to the
non-manure-treated objects increased the soil alkaline extraction residue carbon. On the
manured objects the use of nitrogen increased the soil alkaline extraction residue
carbon, whereas application of phosphorus, potassium and lime had no influence on the
soil alkaline extraction residue carbon.
Influence of fertilization on total soil nitrogen
and its fractions in soil
In the 40-year experiment fertilization with manure increased the total nitrogen
content in soil by 78 % as compared with the objects treated with mineral fertilizers
only (Table 2). In most instances, the effects of fertilization with nitrogen, phosphorus,
potassium and lime on the content of total nitrogen in soil were found similar to the
corresponding fertilization effects on the organic carbon content in soil. The nitrogen
treatment applied to the non-manure-treated objects caused an average 22 % increase in
the total soil nitrogen, whereas the same treatment applied to the manured objects led to
the average increase in that parameter that reached only 12 %. Phosphorus fertilization
resulted in a decrease in total soil nitrogen by 9 % on the objects not treated with
manure and 6 % on the manured ones. In contrast, the use of potassium fertilizers
caused only minor rise in the total soil nitrogen. Liming caused a more important
increase in the total soil nitrogen, which reached 7 % on the manure-treated objects and
14 % on the other ones. The effects of mineral fertilizers on the total soil nitrogen and
its fractions in soil were varied. Similarly to the effects on carbon, the biggest impact on
the accumulation of nitrogen in different fractions of soil organic matter had the manure
fertilization. The content of nitrogen bounded in humin acids, fulvic acids and in the
With
manure
without
manure
0.779
0.814
0.768
0.825
0.797
without K
with K
without lime
with lime
mean
0.773
0.754
without N
with P
0.449
mean
0.839
0.790
with lime
0.820
O.419
without lime
without P
0.460
with N
0.438
with P
with K
0.430
without P
without K
0.494
0.468
with N
0.404
without N
Treatments
Ntot.
[g · kg–1]
11.7:1
11.3:1
12.1:1
11.3:1
12.1:1
11.5:1
12.0:1
11.9:1
11.6:1
14.0:1
13.0:1
15.1:1
14.6:1
13.4:1
14.8:1
13.3:1
13.9:1
14.2:1
C:N
0.476
0.484
0.468
0.467
0.485
0.469
0.483
0.504
0.447
0.266
0.262
0.270
0.274
0.257
0.250
0.282
0.303
0.229
N
[g · kg–1]
7.5:1
7.5:1
7.5:1
7.5:1
7.5:1
7.2:1
7.8:1
7.9:1
7.1:1
9.1:1
9.9:1
8.2:1
9.1:1
9.0:1
9.2:1
8.9:1
9.6:1
8.5:1
C:N
Alkaline extract
0.147
0.142
0.151
0.153
0.143
0.135
0.158
0.167
0.126
0.093
0.097
0.088
0.097
0.088
0.077
0.109
0.113
0.073
N
[g · kg–1]
11.0:1
11.6:1
10.5:1
9.6:1
12.4:1
11.4:1
10.6:1
9.7:1
12.3:1
12.6:1
13.5:1
11.8:1
11.1:1
14.2:1
14.4:1
10.9:1
12.2:1
13.0:1
C:N
Humin acids
0.330
0.342
0.317
0.315
0.344
0.334
0.325
0.338
0.321
0.173
0.164
0.182
0.177
0.169
0.173
0.173
0.190
0.157
N
[g · kg–1]
6.1:1
6.0:1
6.3:1
6.7:1
5.6:1
5.7:1
6.5:1
7.1:1
5.1:1
7.4:1
7.9:1
6.8:1
8.2:1
6.5:1
7.0:1
7.8:1
8.2:1
6.5:1
C:N
Fulvic acids
Table 2
0.320
0.341
0.299
0.347
0.294
0.304
0.337
0.334
0.306
0.183
0.181
0.113
0.186
0.180
0.181
0.186
0.191
0.175
N
[g · kg–1]
18.5:1
17.2:1
19.8:1
16.9:1
20.1:1
19.0:1
18.1:1
18.3:1
18.7:1
22.5:1
16.8:1
28.2:1
23.9:1
21.0:1
24.4:1
20.5:1
22.1:1
22.8:1
C:N
Alkaline extraction
residue
The content of total nitrogen and content organic matter fractions nitrogen in soil and C:N ratio in soil and in organic matter fractions
606
607
compounds remaining after alkaline extraction was higher by 58 to 91 % on the objects
fertilized with manure that on the non-manure-treated ones. Both shares in the total soil
nitrogen: the humin acid nitrogen share and that of nitrogen contained in the
post-alkaline-extraction fraction were slightly lower on the objects fertilized with
manure than on those, which had not been treated with this fertilizer, whereas the fulvic
acids nitrogen share in the total soil nitrogen was slightly higher on the manured
objects. Nitrogen fertilization increased the humin acid nitrogen content in soil by 55 %
on the non-manure-treated objects and by 33 % on the manured ones. It had a smaller
impact on the fulvic acids nitrogen content in soil (21 % and 5 % respectively).
Application of nitrogen to both manured and non-manure-treated objects led to a similar
increase in the content in soil of the nitrogen contained in the post-alkaline-extraction
fraction, which amounted to 9 %. Phosphorus fertilization resulted in an increase in the
humin acid nitrogen content in soil regardless of the use of manure fertilization.
However, it did not affect the fulvic acids nitrogen content in soil, neither on the objects
treated with manure nor on the other ones. Potassium fertilization caused an increase in
the humin acid nitrogen content in soil both on the objects treated with manure and
those, which had not been treated with this fertilizer. It led to an increase in the fulvic
acid nitrogen content in soil on the non-manure-treated objects, whereas it decreased the
fulvic acid nitrogen content in soil on the manured ones. Liming resulted in an increase
in the humin acid nitrogen content in soil and decreased the fulvic acids nitrogen
content in soil on the objects, which had not been treated with manure. Its influence on
the manure-treated objects was opposite. Excepting nitrogen treatment applied in the
form of mineral fertilization, no conclusive results were obtained regarding the effects
of individual nutrients on the nitrogen contained in the post-alkaline-extraction fraction.
Influence of fertilization on C:N ratio in soil
and soil organic matter fractions
Changes in the content of carbon and nitrogen in different soil organic matter
fractions influenced the C:N ratio in soil and in the tested fractions (Table 2). The
disparity in the accumulation of organic carbon and total nitrogen in soil between the
objects fertilized with manure and those not treated with this fertilizer is particularly
interesting. This shows that in sandy-loam soils, which have not been treated with
organic fertilization for years, there is a growing deficit of nitrogen used by crops to
build the yield. This is confirmed by the very high C:N ratio found in the soil applied
only mineral fertilizers, which amounted to 14:1, whereas the one observed in the
manure fertilized soil equaled to 11.7:1. High or low values of the ratio of organic
carbon to total nitrogen in soil went along with similar C:N relations in all studied soil
organic matter fractions. The highest C:N ratio was found in the post-alkaline extraction
fraction, and the lowest one in the fulvic acids. The values of nitrogen content and C:N
ratio in humin and fulvic acids indicate that the vast majority of soil nitrogen is included
in the soil organic matter fractions, which are the most dynamic and susceptible to
mineralization. The much higher C:N ratio in the post-alkaline-extraction fraction,
608
ranging from 18.5:1 to 22.5:1, suggests that compounds contained in this fraction are
less susceptible to microbial decomposition.
Approximately 40 % of total soil nitrogen is deposited in this fraction.
Conclusions
1. Manure fertilization results in an increase in the content of organic carbon and
total nitrogen in soil. Exclusive mineral fertilization with nitrogen, phosphorus and
potassium leads to an increase in the content of both parameters. This increase is lower
than that caused by the manure fertilization.
2. In sandy-loam soil the amount of fulvic acids exceeds the amount of humic acids,
as indicated by the humin-acids-carbon to fulvic-acids-carbon ratio.
3. The manure treatment increases the content of carbon of the following fractions in
soil: the humin acids carbon, the fulvic acids carbon and the soil alkaline extraction
residue carbon. The share of carbon of individual organic matter fractions remains
similar in the soil treated with manure and in that not treated with this fertilizer. It can
be concluded that manure influences the nature and specific properties of the soil
organic matter only to a limited extent, whereas it is essential to its quantitative
development.
4. From among the studied nutrients applied in the form of mineral nutrients and
liming, only nitrogen increases the content of organic carbon and total nitrogen and its
fractions in soil regardless of manure fertilization. The effects of mineral fertilizers on
the content of organic carbon and soil nitrogen and its fractions in soil depend on the
manure fertilization.
5. In sandy-loam soil, which have not been treated with organic fertilization for
years, there exists a growing deficit of nitrogen used by crops to build the yield. This is
confirmed by the very high C:N ratio found in the soil treated only with mineral
fertilizers.
6. About 60 % of total soil nitrogen is included in humin and fulvic acids fractions,
which are the most dynamic and susceptible to mineralization.
References
[1] Jenkinson D. S., Bandbury N. J. and Koleman K.: [In:] Long-term Experiments in Agricultural and
Ecological Sciencies, Leigh R. A. and Johnston A. E. (Eds), Wallingford, Oxfordshire 1994, 117–138.
[2] Körshens M. and Pfefferkom A.: Der Statische Düngungsversuch und andre Feldversuche UFZ-Umweltforsungszentrum Leipzig-Halle GmbH. 1998, 1–56.
[3] Leithold G.: Proc. of the Int. Symp. Long-term Sratic Fert. Exp. 1993, 77–85.
[4] Mercik S. and Stêpieñ W.: Fragm. Agronom. 2005, 22, 189–201.
[5] Maciak Cz. and ¯ebrowski J.: Zesz. Probl. Post. Nauk Roln. 1999, 465, 341–351.
[6] Murawska B. and Spychaj-Fabisiak E.: Folia Univ. Agric. Stetin. 2002, 11, Agricultura, 329–334.
[7] Rabikowska B.: Nawozy i Nawo¿enie 2002, 10(1), 188–197.
[8] Szulc W., £abêtowicz J. and Kuszelewski L.: Zesz Probl. Post. Nauk Roln. 1999, 465, 303–309.
[9] Kalembasa D. and Becher M.: Roczn. Glebozn. 2006, 57, 3/4, 44–54.
[10] Kalembasa D. and Becher M.: Roczn. Glebozn. 2008, 59(2), 98–103.
[11] Kuszelewski L. and ¯urawska A.: Zesz. Naukowe SGGW, Rolnictwo 1967, 9, 53–81.
[12] Kusiñska A.: Roczn. Glebozn. 1996, 47 (Suppl.), 85–96.
609
WP£YW ZRÓ¯NICOWANEGO NAWO¯ENIA MINERALNEGO I ORGANICZNEGO
NA ZAWARTOŒÆ AZOTU I WÊGLA WE FRAKCJACH MATERII ORGANICZNEJ GLEBY
Katedra Nauk o Œrodowisku Glebowym
Abstrakt: Badania nad zawartoœci¹ wêgla i azotu w wybranych frakcjach substancji organicznej gleby
przeprowadzono korzystaj¹c z próbek gleby zebrane w 2005 r. na polu doœwiadczalnym Zak³adu Chemii
Rolniczej SGGW w £yczynie ko³o Warszawy. Po 10 rotacjach zmianowania nawo¿enie obornikiem
zwiêkszy³o zawartoœæ wêgla organicznego i azotu ogólnego w glebie na wszystkich badanych obiektach
doœwiadczenia. Wy³¹czne nawo¿enie mineralne zwiêkszy³o zawartoœæ wêgla organicznego i azotu ogólnego
w glebie na wiêkszoœci obiektów. Jednak przyrost ten by³ mniejszy ni¿ na obiektach nawo¿onych obornikiem.
Nawo¿enie obornikiem zwiêkszy³o zawartoœæ wêgla azotu frakcji materii organicznej w glebie. Udzia³ wêgla
poszczególnych frakcji materii organicznej w wêglu organicznym gleby na obiektach nawo¿onych i nienawo¿onych obornikiem by³ podobny. Wœród sk³adników stosowanych w postaci nawozów mineralnych
tylko azot zwiêksza³ zawartoœæ wêgla organicznego, azotu ogólnego i ich frakcji w glebie niezale¿nie od
nawo¿enia obornikiem. Wp³yw pozosta³ych sk³adników na zawartoœæ wêgla organicznego, azotu ogólnego
i ich frakcji w glebie by³ zró¿nicowany. Stosunek wêgla kwasów huminowych do wêgla kwasów fulwowych
wskazywa³, ¿e w glebie powstawa³o wiêcej kwasów fulwowych ni¿ huminowych. W nienawo¿onej przez
wiele lat obornikiem glebie o sk³adzie mechanicznym piasku gliniastego narasta³ deficyt azotu wykorzystywanego przez roœliny do budowy plonu. Œwiadczy³ o tym szeroki stosunek C:N wynosz¹cy w glebach nawo¿onych wy³¹cznie nawozami mineralnymi 14:1. Wartoœæ tego stosunku w glebach nawo¿onych
obornikiem wynosi³a przeciêtnie 11,7:1.
Wiêkszoœæ azotu w glebie by³a zwi¹zana z kwasami huminowymi i fulwowymi – najbardziej dynamiczn¹
i podatn¹ na mineralizacjê frakcj¹ glebowej materii organicznej.
S³owa kluczowe: doœwiadczenia wieloletnie, nawo¿enie, materia organiczna gleby, wêgiel i azot w glebie
Vol. 18, No. 4
A
2011
Tomasz SOSULSKI1 and Stanis³aw MERCIK1
DYNAMICS OF MINERAL NITROGEN MOVEMENT
IN THE SOIL PROFILE IN LONG-TERM EXPERIMENTS
DYNAMIKA PRZEMIESZCZANIA SIÊ AZOTU MINERALNEGO
W PROFILU GLEBOWYM
W WARUNKACH WIELOLETNICH DOŒWIADCZEÑ NAWOZOWYCH
Abstract: Results presented in this paper come from long term fertilization experiments (5-field crop rotation:
potatoes (30 Mg FYM ha–1), s. barley, r. clover, w. wheat, rye; arbitrary rotation without FYM and without
legumes) carried out in Skierniewice (since 1923). Content of mineral nitrogen (N-NH4+ and N-NO3–) was
measured using Skalar San Plus Flow Analizer, after fresh soil extraction in 0.01 M CaCl2. In all crop rotation
systems and merely all fertilizer treatments the soil content of mineral nitrogen was higher in late autumn than
in spring and than in summer. Among the examined soil profiles the highest content of mineral nitrogen was
shown in the soil treated with FYM (5-field crop rotation – E). The soil content of mineral nitrogen was
significantly higher in the soil fertilized with nitrogen (CaNPK, NPK) than in the unfertilized one (CaPK,
PK). Migration of mineral nitrogen from the top soil layer into deeper layers was bigger in the FYM fertilized
fields with legumes cultivation in crop rotation than in the field not fertilized with manure and without
legumes cultivation.
Keywords: long-term experiment, fertilization, soil nitrogen
Depending on the amount of fertilization, plant species or physicochemical soil
properties, plants uptake usually about 60 % of the fertilizer nitrogen dose [1]. Thus in
the defined agrotechnical and climatic conditions the amount of nitrogen not consumed
by plants may be quite large [2, 3]. In the soils of moderate climate the shift of mineral
nitrogen below the topsoil takes place. The movement of components down the soil
profile is connected with the vertical movement of water. Thus the amount and
distribution of precipitations is the primary factor shaping the dynamics of washing out
the nitrogen [4]. The migration of nitrogen is also greatly affected by the granulometric
composition and type of soil [5], choice of plants in crop rotation [6], management
system of land [7, 8], form and dose of the applied fertilizers [9, 10].
1
Department of Soil Environments Sciences, Warsaw University of Life Sciences, ul. Nowoursynowska 159, 02–686 Warszawa, Poland, phone: +48 22 593 26 30, email: [email protected]
612
Tomasz Sosulski and Stanis³aw Mercik
This paper aims at evaluating changes of mineral nitrogen content in soils with
different chemical properties resulting from 80 year period of various applications of
fertilizers and crop rotation.
The research were carried out in the years 1997–2001 in long term field experiments
performed on Experimental Field in Skierniewice. The Experimetal Field belongs to the
Department of Agricultural Chemistry of Warsaw Agricultural University – SGGW.
Long term fertilizing experiments in that location have been carried out since 1923. The
Experimental Field is located in the Central Poland where the average temperature is
8 oC and rainfall 520 mm (the highest precipitation in July and the lowest in January
and February). The soil in Skierniewice region is podzolic, Haplic Luvisols with the
clay and silt (Ø 0.02 mm) content equals to 15–17 % in Ap, 10–12 % in Eet and 25 % in
Bt soil layers. Plants were cultivated in 2 different crop rotations:
– (A) arbitrary rotation without FYM and without legumes;
– (E) 5-field crop rotation: potatoes (30 Mg FYM ha–1), s.barley, r.clover, w.wheat, rye.
Experiments were conducted in 3 (A) or 5 (E) repetitions. Plots fertilized without and
with nitrogen (CaPK or PK and CaNPK + NPK) were chosen for the evaluation of each
crop rotation. Mineral fertilizers were applied to all crops and within all crop rotations
in the following doses: 90 kg N, 26 kg P and 91 kg K × ha–1. Lime was applied every
four years (1.6 Mg CaO · ha–1) in the fields with A rotations and every five years (2 Mg
CaO · ha–1) in the field with E rotation. Nitrogen in the form of NH4NO3 was applied in
a single dose in the spring before the beginning of vegetation.
Soil samples were collected three times a year during a five year period (1997–2001)
from Ap, Eet and Bt soil layers (0–65 cm): in early spring – before the nitrogen
treatment, in summer – after harvesting and late in the autumn. The content of mineral
nitrogen (N-NH4 and N-NO3) was measured in fresh soil samples using the Skalar San
Plus Analyzer after the fresh soil extraction in 0.01 M CaCl2 (Standard ISO
11261:1995).
The content of total nitrogen in the ploughing soil layer was higher than in the deeper
soil layers. Fertilization with manure and cultivation of legumes in five-crops rotation
(E) increased the total nitrogen content in the studied soil layers in relation to objects
fertilized without manure and without legumes in crop rotation (A). On all objects with
nitrogen fertilization the content of total nitrogen in soil was higher than on objects
without this fertilization. The higher increase of nitrogen content in soil under nitrogen
fertilization was obtained in field A than in field E. The total nitrogen content in soil on
limed objects fertilized with nitrogen (CaNPK) was higher than on objects not treated
with lime (NPK).
The amounts of mineral N in the 0–65 cm layer of the investigated soils varied
depending on the system of fertilization and plant cultivation as well as the time of
Dynamics of Mineral Nitrogen Movement in the Soil Profile in Long-Term Experiments
613
determination from 31–83 kg N · ha–1 in the field E, 18–41 kg N · ha–1 in the field A
(Table 2, 3). Calculating the average from all the fertilization combinations the most
mineral N in the soil profile down to 65 cm was found in the late autumn – at the
beginning of November, less in the spring – prior to the application of nitrogen mineral
fertilizers (March) and the least amount in August – directly after plants harvest (Table
2, 3). According to Labetowicz and Rutkowska, the decrease of the mineral N content in
the soils fertilized with nitrogen observed between the time of fertilizer application and
the time of harvest is caused mainly by the plant uptake of this component [11]. On the
other hand, Fotyma reported that in the Polish soil and climatic conditions the highest
content of mineral nitrogen in soil was obtained after harvest, lower in the late autumn
and the lowest in the early spring [12].
Table 1
–1
The content of total nitrogen [g N · kg ] in the three soil layers (Ap, Eet, Bt) depending on different
ferilization and crop rotation
Crop rotation
Fertilization
Soil layers
E
(five crop-rotation with
FYM and with legumes)
A
(arbitrary rotation without
FYM and without legumes)
Ap
Eet
Bt
Ap
Eet
Bt
PK
NPK
CaPK
CaNPK
—
—
—
0.392
0.279
0.252
0.702
0.296
0.331
0.464
0.238
0.269
0.643
0.305
0.342
0.362
0.219
0.214
0.712
0.315
0.361
0.491
0.277
0.247
Table 2
+
–
The content of mineral nitrogen (N-NH4 +N-NO3 ) in the soil layer of 0–65 cm deep [kg N · ha–1]
in the field with five field crop rotation with legumes and manure (E) at three terms
(March, August, November) depending on long term fertilization
Terms of investigation
(B)
March
August
November
Mean
Fertilization (A)
CaPK
CaNPK
NPK
55.4
33.1
72.6
53.8
79.2
54.5
83.1
72.3
72.2
58.5
68.4
66.4
Mean
LSD
68.9
48.7
74.7
—
A = 2.3
B = 2.3
A/B = 3.4
Table 3
The content of mineral nitrogen (N-NH4+ +N-NO3–) in the soil layer of 0–65 cm deep [kg N·ha–1]
in the fields with arbitrary crop rotation without legumes and manure (A) at three terms
(March, August, November) depending on long term fertilization
Terms of investigation
(B)
March
August
November
Mean
Fertilization (A)
PK
NPK
CaPK
CaNPK
23.6
18.0
24.3
22.0
29.8
27.6
37.4
31.6
25.57
19.79
34.75
26.7
33.0
29.4
41..6
31.2
Mean
LSD
28.0
23.7
32.2
—
A = 1.7
B = 1.7
A/B = 2.9
614
Independently from crop rotation, at all terms of investigations nitrogen fertilization
(CaNPK and NPK) resulted in the increase of the amount of mineral N in the soil as
compared with the objects not fertilized with this element – CaPK and PK (Table 2, 3).
The gains of mineral N content in the soil in combinations of nitrogen fertilization
(CaNPK and NPK) as compared with the control varied in particular fields depending
on the term of determination in the following way: field E 14–65 %, field A 26–54 %.
The described dependence was also observed by Sapek [4] as well as by Labetowicz
and Rutkowska [11]. The effect of liming on the amount of mineral N in the soil during
the whole year was not explicit. In the all investigated fields the amount of mineral N
observed in the limed soils (CaNPK) was significantly higher as compared with the
non-limed (NPK) objects. In the spring the significance of differences between the
amount of mineral N in the limed and non-limed objects was proved in the both fields E
and A. The amounts of mineral N after harvest in the limed and non-limed soils were
similar.
In the soil of the E field (crop rotation with papilionaceous plants and manure) the
amount of mineral N was on the average about twice higher than in the soils not
fertilized with manure in which no legumes plants were cultivated – A. Sosulski et al
report [13] that manure applied every year causes the increase of the mineral N content
in the soil during the whole period of vegetation. In this study large amounts of organic
nitrogen might have come from FYM and post-harvesting legumes residues, which
were mineralized throughout the whole vegetation period over the few years after the
fertilizer application and legumes cultivation.
The results of measurements of the mineral N content at the levels of Ap, Eet and Bt
taken late in the autumn and in the spring allowed for the evaluation of differences in
the translocation of mineral N in the soil profiles of the investigated fields. In November
nearly in all the objects of five-field crop rotation (E) and in the limed objects CaPK
and CaNPK in the field A a bigger amount of mineral N was found in the Ap level than
in the Eet and Bt (Table 4). It was probably caused by an intensive mineralization of
post-harvest remnents and manure taking place in the soil with higher content of total
nitrogen and higher pH. On the other hand, in unlimed objects PK and NPK in the fields
with arbitrary crop rotation (A) the least amounts of the mineral N were observed at the
Ap level and the biggest amounts at the deepest level of the soil profile – Bt. It points to
a smaller amount of post-harvest remnents and their slowed down mineralizationin the
acid soils. Also Fotyma observed [2] a bigger amount of mineral N in the deeper soil
layer than in the top soil during the period from the late autumn and early spring. In her
investigations in the late autumn the most mineral N was in the soil layer of 20–40 cm.
On the other hand in the early spring the amount of mineral N moved down into the soil
profile which was probably caused by leaching out. In our own investigations changes
were observed in the mineral N distribution in the soil profile in all the fields between
the autumn and spring terms of analyses. In the field with five crop rotation (E) in the
early spring a relatively big amount of mineral N was still present in the layer Ap.
Changes in the distribution of mineral N in the profile of the fertilization objects
concerned mainly the level Eet and Bt. As compared with the autumn less of mineral N
was present in the layer Eet and significantly more in the layer Bt. It was most likely the
615
effect of migration down the soil profile of bigger amounts of mineral N from more
sandy Eet layer than from the humus Ap layer. In the field with arbitrary crop rotation
(A) a slightly smaller dynamics of mineral nitrogen migration in the soil profile was
observed than in the five crop rotation field (E). It is revealed by a similar as in the
autumn the spring distribution of mineral N in the soil profile. The decrease of the
content of mineral N in the soil which takes place between the autumn and spring and a
small changes of arrangement of the N mineral in soil levels, was shown that in
arbitrary rotation nitrogen is leached almost evenly from the Ap, Eet and Bt layers.
Table 4
Per cent distribution of mineral N in three layers of the soil profile (Ap, Eet, Bt) and distribution
of N-NO3– in soil N mineral in the field with five crop rotation (E) and with arbitrary crop
rotation (A) in the late autumn and spring depending on long term fertilization
Autumn
Crop rotations
Spring
Soil
% N-NO3– in
Fertilization
layers Nmin in layers Nmin in 0–65 cm
layer
CaPK
E
(five-crop-rotation
CaNPK
with FYM and
with legumes)
NPK
PK
NPK
A
(arbitrary rotation
without FYM and
without legumes) CaPK
CaNPK
Ap
Eet
Bt
Ap
Eet
Bt
Ap
Eet
Bt
Ap
Eet
Bt
Ap
Eet
Bt
Ap
Eet
Bt
Ap
Eet
Bt
47 %
31 %
22 %
41 %
33 %
26 %
46 %
28 %
26 %
24 %
36 %
40 %
31 %
33 %
36 %
38 %
34 %
28 %
39 %
34 %
27 %
63 %
65 %
58 %
49 %
54 %
56 %
61 %
% N-NO3– in
Nmin in layers Nmin in 0–65 cm
layer
40 %
18 %
42 %
44 %
19 %
37 %
39 %
20 %
41 %
31 %
35 %
34 %
39 %
35 %
34 %
38 %
29 %
33 %
39 %
28 %
33 %
35 %
45 %
34 %
38 %
37 %
46 %
51 %
The described changes in the content and distribution of mineral N in the studied soil
profiles between autumn and spring went along with changes in shares of N-NO3– and
N-NH4+ in N mineral in soil. In almost all objects of five-field crop rotation (E) and in
field A with arbitrary rotation the share of N-NO3– in N mineral in the 0–65 cm soil
layer in the autumn was higher than the N-NH4+ share. Only on unlimed object PK the
distribution of N-NO3– in soil profile was similar to that of N-NH4+. The decrease of
mineral nitrogen in soil and changes in its distribution in soil layers between November
and March was accompanied by a decrease in the share of N-NO3– in N mineral in soil
616
profile. This leads to the conclusion, that N-NO3– plays a bigger role in the nitrogen
migration down the soil profile than N-NH4+.
Conclusion
1. Fertilization with farmyard manure and legumes cultivation increases the content
of total nitrogen and mineral nitrogen in the soil layer of 0–65 cm deep.
2. The content of mineral nitrogen in soil is the lowest after the harvest and the
highest in the late autumn. Between the autumn and spring the content of N mineral in
soil decreases.
3. Migration of mineral nitrogen from the top soil layer into deeper layers is bigger in
the FYM fertilized fields with legumes cultivation in crop rotation than in the field not
fertilized with manure and without legumes cultivation.
References
[1] Mercik S., Stêpieñ W. and £abêtowicz J.: Fol. Univ. Agric. Stetin. 2000, 211 Agricultura (84), 317–322.
[2] Fotyma E. and Pietruch Cz.: Zawartoœæ azotu mineralnego w glebach gruntów ornych Polski po zbiorach
roœlin jako wskaŸnik stanu œrodowiska. Wyd. IUNG Pu³awy 1999, pp. 20.
[3] Harasimowicz-Herman G. and Herman J.: Acta Univ. Mazurien., Mat. Konf. Zanieczyszczenie
œrodowiska azotem, Olecko 2005, 203–213.
[4] Sapek A.: Wiadomoœci IMUZ 2000, 22(1), 9–19.
[5] Spychaj-Fabisiak E. and Murawska B.: Zesz. Probl. Post. Nauk Roln. 1994, 414, 21–29.
[6] Peralta J., Jand C.O. and Stockle M.: Agricult. Ecosyst. and Environ. 2002, 88(1), 23–34.
[7] Magesan G.N., White R.E., Scot D.R. and Bolan N.S.: Agricult. Ecosyst. and Environ. 2002, 88(1),
73–77.
[8] Mitchell J.K., Walher S.E., Hirschi M.C., Cooke R.A.C. and Banasik K.: Zesz. Probl. Post. Nauk Roln.
1998, 458, 431–442.
[9] Mazur Z. and Mazur T.: Acta Univ. Mazurien. Mat. Konf. Zanieczyszczenie œrodowiska azotem, Olecko
2005, 173–181.
[10] Shepherd M.: Nawozy i Nawo¿enie 2001, 1(6), 52–62.
[11] £abêtowicz J. and Rutkowska B.: Zesz. Probl. Post. Nauk Roln. 1996, 440, 223–229.
[12] Fotyma E.: Fragm. Agronom. 1995, 3(47), 59–77.
DYNAMIKA PRZEMIESZCZANIA SIÊ AZOTU MINERALNEGO W PROFILU GLEBOWYM
W WARUNKACH WIELOLETNICH DOŒWIADCZEÑ NAWOZOWYCH
Katedra Nauk o Œrodowisku Glebowym,
Abstrakt: Wyniki badañ zamieszczone w pracy zosta³y uzyskane w oparciu o materia³ zebrany trwa³ych
doœwiadczeniach nawozowych (ze zmianowaniem piêciopolowym z roœlin¹ motylkow¹ i obornikiem
i doœwiadczeniu ze zmianowaniem dowolnym bez roœliny motylkowej i bez obornika) prowadzonych od 1923 r.
w Skierniewicach. Zawartoœæ azotu mineralnego w glebie (N-NH4+ and N-NO3–) by³a zmierzona przy u¿yciu
aparatu Skalar San Plus Flow Analizer, po ekstrakcji gleby w 0,01 M CaCl2. Niemal na wszystkich obiektach
nawozowych badanych pól zawartoœæ azotu mineralnego w glebie by³a wiêksza w okresie póŸnej jesieni ni¿
wiosn¹ i latem. Wiêksz¹ zawartoœæ azotu mineralnego stwierdzono w glebie nawo¿onej obornikiem na polu
ze zmianowaniem piêciopolowym ni¿ w glebie pod zmianowanie dowolnym bez roœliny motylkowej i bez
obornika. Zawartoœæ azotu mineralnego w glebie na obiektach nawo¿onych azotem (CaNPK, NPK) by³a
617
wiêksza ni¿ na obiektach nienawo¿onych tym sk³adnikiem (CaPK, PK). Wiêksze przemieszczanie azotu
z wierzchniej warstwy gleby do jej g³êbszych poziomów stwierdzono w warunkach doœwiadczenia ze
zmianowaniem piêciopolowym z roœlin¹ motylkow¹ i obornikiem ni¿ ze zmianowaniem dowolnym bez
roœliny motylkowej i bez obornika.
S³owa kluczowe: doœwiadczenia wieloletnie, nawo¿enie, azot w glebie
Vol. 18, No. 4
A
2011
Tamara PERSICOVA1 and Natalia POSHTOVAYA1
EFFECTIVENESS OF BACTERIAL PREPARATIONS
AND PLANT GROWTH REGULATORS IN THE SEPARATE
AND MIXED CROPS OF OATS, SPRING WHEAT
AND NARROW-LEAVED LUPINE DEPENDING
ON LEVEL OF NITROGEN NUTRITION
EFEKTYWNOŒÆ PREPARATÓW BAKTERYJNYCH
I REGULATORÓW WZROSTU ROŒLIN W SIEWACH CZYSTYCH
I MIESZANYCH OWSA, PSZENICY JAREJ I £UBINU W¥SKOLISTNEGO
W ZALE¯NOŒCI OD POZIOMU ¯YWIENIA AZOTEM
Abstract: The article presents results of research into the influence of bacterial preparations (rizobacterin and
sapronit) and plant regulators of growth (epin and homobrassinolid) on the productivity and quality of grain of
oat, spring wheat and lupine in the separate and mixed crops depending on level of a nitrogen nutrition. We
have established that in the conditions of sod-podzolic soil of average degree cultivation the optimal dose of
nitrogen fertilizer for oat, wheat and mixed crops is 40 kg of acting substance per hectare, for lupine – 10 kg
of acting substance per hectare (at level P60K90). Inoculation of seeds bacterial preparations (rizobacterin and
sapronit) and application of growth regulators (epin and homobrassinolid) in technology of cultivation of oats,
spring wheat, lupine and their mixed crops allows to reduce doses of mineral nitrogen to 30 kg of acting
substance per hectare and to improve quality indicators of grain of studied cultures.
Keywords: oat, spring wheat, narrow-leaved lupine, mixed crops, nitrogen fertilizer, bacterial preparations,
plant growth regulators, efficiency
A strategic problem of scientific researches is search and optimisation of ways of
reception of biologically high-grade and ecologically safe production at the maximum
decrease in negative influence of anthropogenic factors on environment and reduction
of expenses of irreplaceable power resources by its reception.
Cultivation of the mixed crops grain with leguminous cultures promotes the decision
of variety of problems of an agricultural production: preservation and the expanded
reproduction of fertility of soil, ecological, power and albuminous [1]. The mixed crops
1
Education establishment «The Belarusian State Agricultural Academy» Gorky, Belarus, email: [email protected]
620
Tamara Persicova and Natalia Poshtovaya
of these cultures allow increasing efficiency of a field, to receive the balanced forage for
animals, and also to optimize application of mineral fertilizers. Considering biological
advantages of bean cultures, and, in particular, ability to symbiotrophic nitrogen
nutrition, their cultivation is more economic in comparison with other kinds of
agricultural crops [2].
The problem of nitrogen nutrition is connected not only with expenses of nitrogen
mineral fertilizers, but also and that nitrogenous compounds (nitrates) are exposed to
washing away. It is dangerous to environment. Accumulation of nitrates in soil leads to
essential losses of nitrogen as a result of denitrification, which reach 10–35 % of the
total quantity. Unlike nitrogen of mineral fertilizers, the organic nitrogen present in
plants, is ecologically harmless.
To strengthen process of nitrogen fixation it is possible also by using microbiological
preparations: on leguminous – symbiotic, and on grain crops – associative diazotrophic.
Low cost, a high recovery, safety for environment causes their wide application [3]. In
the agrarian-developed countries to 1/3 total areas of grain and leguminous cultures
bacterize diazotrophic preparations, and at the expense of it to 25–40 % reduce use of
expensive and ecologically unsafe mineral nitrogen fertilizers [4].
Also regulators of growth of plants become the important component of modern
“know-how” of production of plant growing. Valuable property of regulators of growth
is that they strengthen receipt of elements of a food in root system [5, 6]. According to a
number of scientists in first half of 21st century by application of physiologically active
substances the basic increase of a crop will be received [7, 8].
The insufficient level of scrutiny of joint application of nitric fertilizers, bacterial
preparations and growth regulators in crops of oats, wheat and lupine confirms necessity
and an urgency of their studying. The purpose of researches: to establish influence of
various doses of nitrogen fertilizers, bacterial preparations, plant growth regulators on
productivity and high quality grain of oats, summer wheat and lupine in the pure and
mixed crops in the conditions of sod-podsolic sandy-loam soils of the north-western of
Belarus.
Field experiments with the legume (narrow-leaved lupine) cv. Pershacvet and oats
cv. Strelec, spring wheat cv. Kontesa were carried out on experimental plot of the
Belarusian state agricultural academy. The soil on experimental plot – sod-podzolic
sandy-loam soil with reaction close to neutral pHKCI = 5.9, low content of humus –
1.7 %, average content of mobile phosphate – 188 mg × kg–1 soil and average content of
mobile potassium – 223 mg × kg–1 soil (index of cultivation 0.72).
The experiment scheme provided studying of efficiency of bacterial preparations
rizobacterin (R) and sapronit (S), plant growth regulators epin (E) and homobrassinolid
(H) depending on doses of nitrogen fertilizers (N10, N40, N70) against P60K90 in the
separate and mixed crops of oats, wheat and lupine.
Mineral fertilizers were brought under preseeding processing of soil. In the
experiment were applied potassium chloride (60 % K2O), ammophos (12 % N and
Effectiveness of Bacterial Preparations and Plant Growth Regulators...
621
42–50 % P2O5), urea (46 % N). Seeds of oats, wheat and lupine processed corresponding bacterial preparations (200 cm3 × ha–1) before sowing. We used 2 % solution of
sodium salt to stick biopreparations into seeds.
Sapronit (S) is a preparation of symbiotic legume bacteria Rhizobium lupini. Organic
sapropel is its substrate-carrier. The quantity of legume bacteria has increased power to
auxin synthesis. Rizobacterin (R) is associative diazotrophe Klebsiella planticola (titre
2–2.5 billion viable cells/cm–3) that affects the fixation of air nitrogen, biosynthesis of
indoleacetic acid and suppresses the vital activity of root pathogenesis.
When the legume was in phase of budding and oats and wheat was scooting we
applied growth regulators for non-soil dressing in the following doses: epin –
50 cm–3 × ha–1, homobrassinolid – 25 cm3 × ha–1. Epin, 0.025 % is a solution prepared
on the basis of epibrassinolid that belongs to natural phytohormones. It is a bioregulator
of the plant growth that decreases the plant stress and increases plant resistance on
unfavorable environment conditions (climatic conditions, diseases, pesticides etc).
Homobrassinolid 0.125 % is a preparation that belongs to recently discovered new class
natural phytohormones – brassinosteroids.
The maintenance of a crude protein paid off multiplication maintenances of the
general nitrogen defined by method of Kjeldahl, on recalculation factor – 6.25.
Exit of a crude protein in recalculation on dry matter defined on the basis of
percentage of fiber in plants and their productivity, increased by factor 0.86 [10].
The economic estimation of cultivation of studied cultures in experience by us has
been spent on the basis of cost of the received crop and actual expenses taking into
account existing regulations concerning the technology of cultivation [9]. Agronomical
efficiency of fertilizers was defined by the standard method developed at the Institute of
Agricultural Chemistry and Soil Science of Belarus [10]. The method essence consists
that calculation of a predicted crop taking into account quality of soil and amount of
brought fertilizers in the beginning is made, then are defined an increase in crop from
the brought fertilizers and an actual reimbursement of fertilizers.
Statistical processing of the received results was carried out by a method of the
dispersive analysis with use of computer programs Excel and Statistica 7.0.
As a result of the researches it is established, that studied cultures positively react to
entering of mineral nitrogen. Optimum doses of entering of mineral nitrogen in crops of
oats, spring wheat, narrow-leaved lupine and their mixes were defined by a grain yield
increase. For one-specific crops of oats by an optimum dose of nitrogen at level P60K90
– 70 kg of acting substance per hectare, for wheat of 40 kg, where productivity of these
cultures averages 3.83 and 4.01 Mg × ha–1, at a reimbursement of grain of 1 kg NPK of
7.9 and 8.7 kg. The productivity increase to N10 is received at oats – 0.57 Mg × ha–1 and
wheat – 0.31 Mg × ha–1. For pure crops of lupine an optimum dose of nitrogen is – N10
where productivity on the average for three years of researches has made 2.3 Mg × ha–1,
a reimbursement of 1 kg NPK 5.5 kg grains (Table 1). The further increase in a dose of
mineral nitrogen has not led to increase of productivity of this culture.
3.80
3.43
3.94
3.74
3.65
Oats + H
Oats (R)
Oats (R)+E
Oats (R)+H
Average
0.48
0.68
0.17
0.54
0.38
Increase
8.6
8.8
9.5
8.1
8.9
8.6
7.7
Reimbursement of
1 kg
NPK
12.6
13.5
12.9
12.8
13.8
12.4
10.5
Crude
protein [%]
3.94
3.90
3.92
4.05
4.18
3.95
S. wheat + E
S. wheat + H
S. wheat (R)
S. wheat (R)+E
S. wheat (R)+H
Average
0.48
0.35
0.22
0.20
0.24
9.7
10.2
9.9
9.6
9.5
9.6
9.1
14.5
15.9
15.1
13.8
14.6
14.6
12.5
2.64
2.32
2.47
2.49
2.48
2.45
N. lupine + E
N. lupine + H
N. lupine (S)
N. lupine (S)+E
N. lupine (S)+H
Average
0.18
0.19
0.17
0.02
0.34
5.8
5.9
5.9
5.9
5.5
6.3
5.5
33.9
34.6
34.9
34.4
33.5
33.6
32.3
0.71
0.74
0.75
0.73
0.67
0.76
0.64
0.49
0.57
0.53
0.47
0.49
0.49
0.40
0.39
0.43
0.45
0.38
0.45
0.39
0.29
Exit of
a crude
protein
[Mg
× ha–1]
S. wheat – spring wheat; N. lupine – narrow-leaved lupine.
LSD 05: (A) – 0.47; (B) – 0.65; (AB) – 0.69
2.30
N. lupine
LSD 05: (A) – 0.46; (B) – 0.54; (AB) – 0.79
3.70
S. wheat
LSD05: (A) – 0.42; (B) – 0.74; (AB) – 0.76
3.26
3.64
Oats + E
Productivity
[Mg
× ha–1]
Oats
Variant
(factor A)
Background 1 – N10P60K90
320.7
320.9
319.7
322.8
320.3
319.8
320.7
102.5
102.6
102.6
101.5
102.5
102.5
103.0
64.7
65.0
65.0
64.2
64.8
65.0
64.4
Security feed
unit, g
digestible protein
93.8
92.4
93.2
100.2
81.7
106.8
88.4
180.8
190.2
181.2
186.6
174.7
177.5
174.8
75.1
74.0
88.0
71.5
79.5
72.0
65.8
Profitability [%]
2.74
3.23
2.86
2.74
2.54
2.54
2.51
4.29
4.81
4.70
4.05
4.17
4.06
3.95
4.20
4.15
4.26
4.12
4.41
4.30
3.95
0.72
0.35
0.23
0.04
0.04
0.86
0.75
0.10
0.22
0.11
0.20
0.31
0.17
0.46
0.35
ProducIntivity
crease
[Mg
× ha–1]
6.1
7.1
6.3
6.1
5.6
5.6
5.5
9.8
10.9
10.7
9.2
9.5
9.2
9.0
9.2
9.1
9.4
9.1
9.7
9.4
8.7
Reimbursement of
1 kg
NPK
34.2
34.7
35.1
34.5
33.5
33.8
33.4
14.3
14.7
14.8
13.3
15.4
14.4
13.2
13.3
13.7
13.5
13.4
13.2
12.4
11.1
Crude
protein [%]
0.81
0.96
0.86
0.81
0.73
0.74
0.72
0.53
0.61
0.60
0.46
0.55
0.50
0.45
0.48
0.49
0.49
0.47
0.5
0.46
0.38
Exit of
a crude
protein
[Mg
× ha–1]
319.9
320.1
320.4
320.4
319.9
319.9
318.6
102.9
102.6
102.7
103.4
102.6
102.6
103.6
64.1
65.0
64.8
63.0
64.9
65.0
61.5
Security feed
unit, g
digestible protein
Levels of a nitrogen nutrition (factor B)
90.6
137.0
109.0
67.5
88.1
88.1
52.9
180.6
207.8
200.7
169.3
170.2
163.1
172.5
80.3
77.1
81.8
73.2
90.8
86.0
72.6
Profitability [%]
2.17
2.32
2.16
2.04
2.23
2.20
2.06
4.18
4.43
4.57
3.84
4.25
4.19
3.78
4.10
4.23
4.25
3.95
4.12
4.24
3.83
0.26
0.1
–
0.17
0.14
0.65
0.79
0.06
0.47
0.41
0.4
0.4
0.12
0.29
0.41
ProducIntivity
crease
[Mg
× ha–1]
3.7
4.0
3.7
3.5
3.8
3.8
3.5
8.9
9.4
9.4
8.2
9.1
8.9
8.1
8.4
8.7
8.8
8.2
8.5
8.8
7.9
Reimbursement of
1 kg
NPK
33.9
34.2
34.3
33.8
33.8
33.5
33.7
14.9
15.2
15.7
15.4
14.5
14.6
14.4
14.2
14.3
14.4
14.2
13.9
13.5
13.1
Crude
protein [%]
0.63
0.68
0.64
0.59
0.65
0.63
0.60
0.54
0.58
0.62
0.51
0.53
0.53
0.47
0.50
0.52
0.53
0.48
0.49
0.49
0.43
320.5
320.3
321.1
319.1
320.4
320.3
321.9
102.7
102.5
102.6
102.8
102.5
102.6
103.1
64.0
65.0
65.0
62.8
64.5
63.7
62.7
SecuriExit of
ty feed
a crude
unit, g
protein
digesti[Mg
ble
pro× ha–1]
tein
Efficiency of application nitrogen fertilizers, bacterial preparation and growth regulators in crops of oats, spring wheat and narrow-leaved lupine (An average 2006–2008)
52.7
61.5
50.4
47.7
56.6
54.5
45.4
132.4
129.4
136.6
137.4
122.7
119.0
149.1
66.1
66.7
67.5
66.6
64.4
69.2
62.2
Profitability [%]
Table 1
622
623
In our researches for mixed crops (oats + spring wheat + narrow-leaved lupine) an
optimum dose of nitrogen in the basic entering is N40 where productivity has made
3.89 Mg × ha–1 and an increase to N10 – 0.37 Mg × ha–1 at a reimbursement of 1 kg NPK
of 8.9 kg grains (Table 2). The further increase in a dose of nitrogen fertilizers in mixed
crops is inexpedient, since, it does not lead to increase in productivity against P60K90.
On the average for years of researches productivity of a mix of oats, wheat and lupine
was at level of one-specific crops of grain crops.
As researches have shown the efficiency of plant growth regulators depended on
level of a nitrogen nutrition and bacterial preparations in the one-specific and mixed
crops of studied cultures. On the average for three years of researches efficiency of
growth regulators in oats crops above against N40, the productivity increase has made
from 0.35 to 0.46 Mg × ha–1, a reimbursement of grain of 1 kg NPK of 9.4 and 9.7 kg,
profitability of 86.0 and 90.8 %. With increase in a dose of nitrogen fertilizers
efficiency of growth regulators decreases, the productivity increase fluctuates from
0.26–0.41 Mg × ha–1, a reimbursement of grain of 1 kg NPK of 8.5 and 8.8 kg,
profitability of 69.2 and 64.4 %. Highly effectively joint application of rizobacterin for
preseeding processing of seeds and growth regulators in an exit phase in a tube of oats
against N10: the increase of productivity from epin has made 0.68 Mg × ha–1,
a reimbursement 1 kg NPK 9.5 kg grains, profitability of 88.5 %; homobrassinolid –
0.48 Mg × ha–1, at a reimbursement 8.8 kg grain and profitability at level of 74 %.
Whereas with increase in a dose of mineral nitrogen to 40 kg of acting substance per
hectare. Additional gathering of grain has made 0.31 Mg × ha–1 and 0.2 Mg × ha–1,
a reimbursement of grain of 9.4 and 9.1 kg, profitability of 81.8 and 77.1 %; against N70
– 0.42 and 0.4 Mg × ha–1, a reimbursement of grain of 1 kg NPK of 8.8 and 8.7 kg,
profitability of 67.5 and 66.7 % accordingly.
Thus, in one-specific crops of oats processing of seeds before crops of rizobacterin
and spray dressing of epin – the highly effective reception, allowing to increase
productivity of oats against N10 by 0.68 Mg × ha–1, at a reimbursement 1 kg NPK 9.5 kg
grains, profitability of 88.5 %.
The greatest increase of productivity in spring wheat crops at application of studied
growth regulators was against N70 – 0.1 and 0.47 Mg × ha–1, however on a
reimbursement of 1 kg NPK and profitability more effective have appeared regulators
of growth against N10 (a reimbursement 1 kg NPK 9.6 and 9.5 kg of grain, profitability
of 177.5 and 174.7 %). Against N40 at inoculation seeds before crops of rizobacterin and
spray dressing in an exit phase in a tube epin and homobrassinolid the productivity
increase has made 0.75 and 0.86 Mg × ha–1, a reimbursement of grain of 1 kg NPK of
10.7 and 10.9 kg, profitability of 200.7 and 207.8 %. Against N70 additional gathering of
grain from joint application rizobacterin and epin has made 0.79 Mg × ha–1,
homobrassinolid – 0.65 Mg × ha–1, a reimbursement of grain of 1 kg NPK of 9.4 kg,
profitability of 136.6 and 129.4 %, whereas, against N10 a productivity increase – 0.35
and 0.48 Mg × ha–1, at profitability of 181.2 and 190.2 %. Thus, application of growth
regulators stimulating action and bacterial preparations has provided the best indicators
of efficiency in variants without additional entering of nitrogen, and also against N40.
3.8
3.7
3.6
4.0
3.8
3.7
Oats + S. wheat
+ N. lupine + E
Oats + S. wheat
+ N. lupine + H
Oats (R) + S. wheat
(R) + N. lupine (S)
Oats (R) + S. wheat
(R) + N. lupine (S)
+E
Oats (R) + S. wheat
(R) + N. lupine (S)
+H
Average
0.3
0.5
0.1
0.2
0.3
9.0
9.1
9.1
8.7
9.1
9.4
8.6
14.5
15.9
15.1
13.8
14.6
14.6
13.1
S. wheat – spring wheat; N. lupine – narrow-leaved lupine.
0.47
0.52
0.51
0.42
0.47
0.48
0.40
117.0
116.4
115.7
115.4
120.5
121.1
113.0
152.1
153.0
161.6
147.7
149.5
157.5
143.3
4.0
4.0
4.1
3.8
4.1
4.4
3.9
0.1
0.2
–
0.2
0.5
9.8
10.1
10.1
10.1
9.4
10.1
8.9
16.0
16.1
16.7
15.4
16.3
16.4
15.3
0.55
0.53
0.58
0.50
0.58
0.62
0.51
ReExit of
imburCrude a crude
seprotein protein,
ment
[%]
[Mg
of 1 kg
× ha–1]
NPK
LSD 05: (A) – 0.46; (B) – 0.39; (AB) – 0.64
3.5
ProductiviInty
crease
[Mg
× ha–1 ]
Oats + S. wheat
+ N. lupine
Variant
(factor A)
ReExit of
imburCrude a crude
seprotein protein
ment
[%]
[Mg
of 1 kg
× ha–1]
NPK
SecuriProty feed
Profit- ductiviunit, g
Inability
ty
digesticrease
[%]
[Mg
ble pro× ha–1 ]
tein
121.1
117.5
118.5
118.0
125.4
121.3
125.6
156.3
147.9
150.4
150.5
156.4
176.3
156.3
3.8
3.7
3.9
3.7
3.8
3.8
3.5
0.2
0.4
0.2
0.3
0.3
SecuriProty feed
Profit- ductiviunit, g
Inability
ty
digesticrease
[%]
[Mg
ble pro× ha–1]
tein
Levels of a nitrogen nutrition (factor B)
Efficiency of application of nitrogen fertilizers, bacterial preparation and growth regulators in the mixed crops
(Oats + spring wheat + narrow-leaved lupine) (an average 2006–2008)
8.1
8.0
8.7
7.8
8.2
8.1
7.5
16.2
15.8
16.4
15.9
15.5
15.6
15.7
0.53
0.52
0.57
0.50
0.54
0.54
0.48
ReExit of
imburCrude a crude
seprotein protein
ment
[%]
[Mg
of 1 kg
× ha–1]
NPK
117.7
116.3
120.9
120.7
120.1
117.3
110.8
110.7
115.8
123.3
98.4
87.7
122.2
116.7
Security feed
Profitunit, g
ability
digesti[%]
ble protein
Table 2
624
625
In crops of narrow-leaved lupine the authentic increase in productivity from
application of epin has been received against N10 – 0.34 Mg × ha–1, at a reimbursement
of grain of 1 kg NPK of 6.3 kg, profitability of 106.8 %. Application of sapronit for
preseeding processing of seeds and application of growth regulators for spray dressing
against N40, an increase of productivity from 0.35 to 0.72 Mg × ha–1, a reimbursement of
grain of 6.3 and 7.1 kg, profitability of 109.0 and 137.0 % is highly effective.
Efficiency of regulators of growth in the mixed crops above against N40, the increase
of productivity from epin – 0.54, homobrassinolid – 0.22 Mg × ha–1, thus a
reimbursement of 1 kg NPK has made 10.1 and 9.4 kg of grain, profitability of 176.3
and 156.4 %. Whereas, against without additional entering of mineral nitrogen, an
increase – 0.32 and 0.2 Mg × ha–1, a reimbursement – 9.4 and 9.1 kg of grain,
profitability of 157.5 and 149.5 %; against 70 kg of acting substance per hectare.
Nitrogen additional gathering of grain – 0.28 and 0.29 Mg × ha–1, a reimbursement –
1 kg NPK of grain of 8.1 and 8.2 kg, profitability of 122.2 and 87.7 % accordingly.
From inoculation of seeds and application of epin against N10 in the sum the
productivity increase has made 0.43 Mg × ha–1, against N70 – 0.53 Mg × ha–1, at
a reimbursement of grain of 9.4 and 8.7 kg, profitability of 161.6 and 153.0 %.
Thus, application of bacterial preparations and growth regulators on sod-podsolic soil
of average degree cultivation – effective reception in technology of cultivation of oats,
spring wheat and narrow-leaved lupine in the pure and mixed crops.
In the conditions of constant deficiency of fodder fiber the albuminous characteristic
of forages has great value [11]. On the average for years of researches the maintenance
of a crude protein in oats grain has made 11.05–13.01 %, in wheat grain –
11.60–14.35 %, lupine – 31.29–34.29 %, in mix grain – 13.03–15.59 % at gathering
accordingly 0.35–0.42, 0.45–0.51, 0.48–0.64 and 0.42–0.51 Mg × ha–1 (Table 1–2).
It is necessary to notice, that food conditions, and in more degrees nitrogen,
differently influence not only size, but also on quality of a crop. In our researches
entering of nitrogen fertilizers also has made essential impact on the maintenance of a
crude protein. In oats and spring wheat grain the given indicator increases from 0.93
(between N10 and N40) and 1.03 (between N40 and N70) to 1.96 % (between N10 and N70)
in oats grain; from 1.54 (between N10 and N40) and 1.17 (between N40 and N70) to
2.71 % (between N10 and N70) in spring wheat grain. In grain narrow-leaved lupine the
tendency of decrease in the maintenance of a crude protein with increase of a dose of
nitrogen fertilizers on 1.3–3.0 % (Table 1), on the contrary, is observed. Hence, at
inclusion in a mix narrow-leaved lupine updating of doses of nitrogen is necessary.
According to researches it is dose N40 of acting substance per hectare where the
maintenance of a crude protein in grain makes 15.59 %, and an exit of a crude protein –
0.51 Mg × ha–1.
Against N70 inoculation of seeds oats rizobacterin and application of growth
regulators the maintenance of a crude protein has made 14.4 and 14.3 %, against N40 –
13.5 and 13.7, N10 – 12.9 and 13.5 %, security of fodder unit of digestible protein – 65
g. The maintenance of a crude protein in wheat grain at inoculation of seeds a bacterial
preparations and application epin and homobrassinolid for spray dressing against N70
626
was 15.7, 15.2 %, security of fodder unit of digestible protein 102.6 and 102.5 g; against
N40 – 14.8 and 14.7 %, security of fodder unit of digestible protein – 102.7 and 102.6 g.
At application against N10 of inoculation seeds and growth regulators the maintenance
of a crude protein in grain of narrow-leaved lupine has made 34.9 and 34.6 %, against
N40 – 35.1 and 34.7 %, security of fodder unit of digestible protein 319.7–321.1 g.
In the mixed crops these indicators above against N40 also have made at application
of bacterial preparations and growth regulators of 16.1–16.7 % and 117.5–118.5 g of
digestible protein. Thus, with increase in the level of nitrogen nutrition in crops
narrow-leaved lupine and mixed crops it is not marked improvements of quality of
grain. Hence, at application of epin in the mixed crops it is possible to lower nitrogen
doses on 30 kg × ha–1 of acting substance. And to receive productivity at level of
4.43 Mg × ha–1, at security of 1 fodder unit of digestible protein – 121.3 g.
Conclusions
1. Efficiency of bacterial preparations and growth regulators in the pure and mixed
crops of oats, wheat and lupine depends on level of a nitrogen nutrition and crops kind.
2. In pure crops of oats processing of seeds before crops of rizobacterin and spray
dressing in an exit phase in a tube epin on background N10 is highly effective.
3. For crops of wheat against N40 it is highly effective preseeding inoculation
rizobacterin and spray dressing homobrassinolid.
4. In technology of cultivation narrow-leaved lupine at processing of seeds before
crops sapronit and spray dressing in a phase budding homobrassinolid a dose of mineral
nitrogen of 40 kg × ha–1 of acting substance it is necessary to consider optimum.
5. In the mixed crops against N40 application of growth regulator epin for spray
dressing is highly effective.
6. Application of bacterial preparations and growth regulators in technology of
cultivation of oats, spring wheat and narrow-leaved lupine in the pure and mixed crops
allows to reduce doses of mineral nitrogen to 30 kg × ha–1 of acting substance and to
improve quality indicators of grain of studied cultures.
References
[1] Benz V. A.: Polyspecific crops in feed processing: the theory and practice. Russ. Acad. of Agricult. Sci.,
Siber. Inst. of Fodder, Novosibirsk 1996, 225.
[2] The mixed crops of annual forage crops. Recommendations, Minsk 1973, 17.
[3] Bazilinsky M.B.: Bioudobrenija, Minsk. Science 1989, p. 126.
[4] Suhovitsky L.A.: Biological nitrogen: results and prospects of development of researches at the Institute
of Microbiology National Academy of the Sciences of Belarus. Problems of a food of plants and use of
fertilizers in modern conditions. Hata, Publishing House, Minsk 2000, 505–508.
[5] Ðrusàñîvà L.D.: Regulator of growth in plant growing. Agricult. Biol. 1984, 3, 3–13.
[6] Kudearov G.R. and Usmanov I.U.: Íormones and a mineral feeding. Physiol. Biochem. of Crop Plants.
1991, 23(3), 232–244.
[7] Melncov N.N.: World’s millers consumption of pesticides in 1989 and prospect for 1995. Agrochemistry
1991, 5, 138.
[8] Zaharenko V. A.: Pesticides in the integrated protection of plants. Agrochemistry 1992, 12, 92–105.
627
[9] Gusakov V.G. Organizational-technological specifications of cultivation of agricultural crops: The
collection of branch regulations. Science, Minsk 2005, pp. 462.
[10] Vildflush I.R., Kukresh S.P. and Tsyganov A.R.: Agrochemistry. Studies, Minsk 2000, pp. 319.
[11] Kukresh L.V.: To a problem of manufacture of fodder fiber. Agricult. Protect. of Plants 2004, 6, 3–5.
EFEKTYWNOŒÆ PREPARATÓW BAKTERYJNYCH I REGULATORÓW WZROSTU ROŒLIN
W SIEWACH CZYSTYCH I MIESZANYCH OWSA, PSZENICY JAREJ I £UBINU
W¥SKOLISTNEGO W ZALE¯NOŒCI OD POZIOMU ¯YWIENIA AZOTEM
Katedra Chemii Rolnej
Bia³oruska Pañstwowa Akademia Rolnicza w Gorkim, Bia³oruœ
Abstract: W publikacji zosta³y przedstawione wyniki badañ wp³ywu bakteryjnych preparatów (rizobakterin
i sapronit) i regulatorów wzrostu roœlin (epin i homobrassinolid) na plon i jakoœæ ziarna owsa, pszenicy jarej
i ³ubinu w jednogatunkowych i mieszanych siewach w zale¿noœci od poziomu nawo¿enia azotowego.
Ustalono, ¿e w warunkach gleb darniowo-bielicowych o œrednim stopniu wzrostu bakterii, optymalna
dawk¹ azotu dla owsa, pszenicy jarej i mieszanek tych kultur na poziomie P60K90 by³a 40 kg × ha–1, dla ³ubinu
– 10 kg × ha–1. Inokulacja nasion bakteryjnymi preparatami (rizobakterin i sapronit) i zastosowanie
regulatorów wzrostu (epin i homobrassinolid) w technologii uprawy owsa, pszenicy jarej, ³ubinu i mieszanek
tych kultur pozwala zmniejszyæ dawki azotu mineralnego do 30 kg × ha–1 i poprawiæ jakoœciowe
charakterystyki ziarna badanych kultur.
S³owa kluczowe: owies, pszenica jara, ³ubin w¹skolistny, mieszane agrofitocenozy, nawozy azotowe,
bakteryjne preparaty, regulatory wzrostu, efektywnoœæ
A
Vol. 18, No. 4
2011
Ewa SPYCHAJ-FABISIAK1, Jacek D£UGOSZ2
and Krzysztof PI£AT1
SPATIAL VARIABILITY OF TOTAL NITROGEN
IN THE SURFACE HORIZON
AT THE PRODUCTION FIELD SCALE
ZMIENNOŒÆ PRZESTRZENNA ZAWARTOŒCI AZOTU OGÓ£EM
W POZIOMIE POWIERZCHNIOWYM
W SKALI POLA PRODUKCYJNEGO
Abstract: Soil total nitrogen does not come under so great temporal changes as its mineral forms, but it could
be spatially differentiated. Spatial variability of total nitrogen could occur in the region scale as well as in the
microscale that is to say within production field scale. For agricultural practice very important is to know
spatial variability of its nitrogen form in the field scale since it could be very important to optimization of
fertilization. That is why the objective of this study was to estimate total nitrogen spatial variability in the
field scale. To this end 16.5 hectare field after winter wheat cultivation was chosen and soil samples from 47
individual points were collected in spring every 50 m. Total nitrogen was determined by Kjeldahl method. On
the basis of total N content results empirical variograms were drawn with SURFER 8.0 software. On the
ground of variograms, mathematical models and raster maps illustrating the distribution of investigated total
nitrogen content in the field scale were drown. Basic statistic calculations were done with the use of
STATISTICA 8.0 software. Results showed differentiated concentration of total nitrogen content in the humic
horizon of investigated soil (0.78–1.11 g × kg–1). Small differentiation of determined nitrogen could be
confirmed by low standard deviation (0.078) and low correlation coefficients (8.44 %). Geostatistical analysis
proved that surface layer nitrogen did not occur full dispersion what was confirmed by nugget effect
amounting 0.001 (g/kg)2 with the sill variance accounted for 0.006 (g/kg)2. The large range of 212 m
evidenced that the correlation between total nitrogen content is bigger than distances between samples points.
Proper adjustment of models (spherical and nugget effect) was confirmed also by the variance calculated
(0.006 [g/kg]2), similar to sill variance defined on the ground of those models.
Keywords: spatial variability, total nitrogen, production field, surface horizon
1
Department of Agrarian Chemistry, University of Technology and Life Sciences in Bydgoszcz, ul.
Seminaryjna 5, 85–326 Bydgoszcz, Poland, phone +48 52 374 91 00, fax +48 52 374 91 03, email:
[email protected]
2
Dept. of Soil Science and Soil Protectin, University of Technology and Life Sciences in Bydgoszcz, ul.
Bernardyñska 6, 85–029 Bydgoszcz, Poland, phone +48 52 374 95 12, fax +48 52 374 95 05, email:
[email protected]
630
Ewa Spychaj-Fabisiak et al
Soil fertility, among others, is determined by organic matter content [1, 2], which
except for many functions is the reservoir of biogenic components for plants. One of
them is nitrogen which accounts for 0.02–0.40 % of the topsoil [3]. Nitrogen occurs
there mainly in organic compounds and only about 10 % constitutes mineral forms [4].
Organic forms of nitrogen become available for plants during organic matter decomposition processes. Nowadays, when well-balanced and ecological agricultural is
promoted, not only qualification of the specific biocomponent content (ie total nitrogen)
but also its spatial variability in the field scale is important [5].
It is even more significant in the context of more and more widely popular precision
agriculture, in which one of the important elements is a practical consideration of
a variability occurring in the area of the very specific arable field. That is why it is
necessary to evaluate, at least preliminary, changeability of specific soil parameters and
transfer these data to an applicable measure, such as precision sampling and the
magnitude of the indicated classes.
Therefore, the objective of this study was to evaluate the spatial variability of total
nitrogen at the production field scale. Moreover, an attempt to mark the distance
between sampling points for total nitrogen variability determination has been done.
The research was conducted on the 16.5 hectare field under cultivation localized near
the Lobdowo village (Cuiavia-Pomerania province). The field was covered by Alfisols
classified to IIIa and IVa classes according to soil classification (land-capability
taxation). Most of the surface of the research area was classified as a fine sandy loam
according to PN 04033 except for a small area, which was covered by surface layer
classified as a fine sand. Ranges and mean values of basic parameters of research area
are shown in Table 1.
Table 1
Ranges and means of some properties of the investigated area
C-org
Parameter
Min. – Max
Mean
Clay fraction
g × kg–1
8.16 – 15.15
11.66
6 – 15
9.3
pH
CEC
1 M KCl
mmol(+) × kg–1
5.13 – 7.1
6.12*
4.93 – 11.50
7.15
* Geometric mean.
The field under study was prepared for corn cultivation with winter wheat as the
forecrop. Farmyard manure was applied at the dose 30 Mg × ha–1, while nitrogen
fertilization as urea (330 kg × ha–1) was used in autumn. In spring, before sowing
of corn, soil samples were collected from 47 points of the soil surface layer.
Sampling points were localized by the Magellan GPS system and distributed every 50 m
(Fig. 1). Each soil sample accounted for the mean value of 20 individual samplings
done by the Egner sampling device. Soil samples were dried and passed through a 2 mm
Spatial Variability of Total Nitrogen in the Surface Horizon...
631
N
Fig. 1. Localization of sampling points on the research field
sieve. The fraction below 2 mm was analyzed for granulometric composition by a
standard Cassagrande method as modified by Proszynski, pH in 1 M KCl, organic
carbon content by volumetric method with 0.4 M K2Cr2O7 and total nitrogen by
Kjeldahl method.
The results were evaluated with the use of classical statistical methods (STATISTICA
v. 8.0 software) calculating arithmetic (AM) and geometric (GM) means, median (Me)
standard deviation (SD), coefficient of variation (CV%), as well as skewness (Sw),
kurtosis (K) and variance. Geostatistical calculations were done with the use SURFER
8.0 of Golden Software and they included empirical semivariograms graphs and
theoretical mathematical model of variograms. On the ground of semivariograms raster
maps illustrating the spatial variance of determined total nitrogen were drawn. The
method of point kriging was adapted to the date estimation [6].
The analyses showed that total nitrogen content in the surface horizon of the
investigated production field disclosed a small spatial variability. Total nitrogen
concentrations in the surface layer ranged 0.775–1.110 g × kg–1, with mean value 0.924
g × kg–1 (Table 2). The mentioned values fit in the range obtained in the surface area of
the Cuiavia-Pomerania region soils [7]. However, comparison of mean value of total
nitrogen content determined in the investigated area showed that it was lower about
0.746 g × kg–1 than the mean value obtained for soils of the region whereas mean total
nitrogen value calculated for the investigated field was lower about 0.506 g × kg–1 than
the amount determined in soils samples collected from the field located at the
Sepopolska Plain [8].
A small variability of N-total obtained for the analyzed soil was confirmed by a low
standard deviation value (0.078 g × kg–1) and coefficient of variation (8.4%) (Table 1).
632
Field spatial variability of total nitrogen content was lower than that of organic
carbon, what was shown by a higher CV value (14.9 %) (data not shown). Similar
values of arithmetic and geometric means as well as similar to normal total N
distribution (K = 0.158) (Table 2) gave evidence for the lack of values differed from the
mean. Total nitrogen content distribution showed a small right-sited asymmetry, what
indicated that a large part of the results were lower than the mean and was confirmed by
the median value lower than the mean (Table 2). According to the results reported by
Cambardella et al [9] and Stenger et al [10] the occurrence of asymmetry in total N
distribution is typical.
Table 2
Some statistical and geostatistical parameters of total nitrogen content
Parameter
n
Total nitrogen
47
Min.
0.775 g × kg–1
Max
1.11 g × kg–1
Arithmetic mean (AM)
0.924 g × kg–1
Geometrical mean (GM)
0.921 g × kg–1
Median
0.920 g × kg–1
Standard deviation (SD)
0.078 g × kg–1
Coefficient of variation (CV%)
8.4 %
Skewness
0.395
Kurtosis
0.158
Variance
Model
0.006
spherical, nugget effect
Nugget variance (C0)
0.001 (g × kg–1)2
Total sill variance Cw = (C0 + C)
0.006 (g × kg–1)2
Nugget effect (C0 / (C0 + C)) × 100
16.7 %
Range m
212 m
A theoretical mathematical model was designed to show a small N-total spatial
variability on the basis of empirical semivariograms and small values of total sill
variance (0.006 [g × kg–1]2) were obtained. The sill variance contained the nugget
variance as well, which amounted for N-total (0.001 [g × kg–1]2) (Fig. 2). It accounted
for 16.7 % of total sill variance (Table 2) and was caused by the occurrence of
short-range influence variability due to the existence of microstructures in the spatial
distribution (ie organic matter centers). The nugget effect was confirmed by Cambardella
et al [9] and Stenger et al [10]. The range of semivariogram, defined as a distance of
correlations between neighbouring sampling points [11], for investigated area amounted
212 m (Fig. 2). The raster maps drawn on the basis of calculated semivariograms
showed that most of the surface layer of the investigated field contained from 0.9 to 1.0
g × kg–1 N total. Only small areas near the east and south-west border of the field had
lower total nitrogen content (Fig. 3).
633
0.008
28
46
31
0.007
24
14
43
17
11
0.006
40
33
24
Variogram
0.005
12
16
39
0.004
30
34
18
0.003
4
0.002
0.001
0
0
20
40
60
80
100
120
140
160 180
200
Range [m]
Fig. 2. Empirical semivariogram of total nitrogen content with estimated theoretical model
1.05
1
0.95
0.9
0.85
0.8
g/k g N
0
50
100
150
200
250
300
350 m
Fig. 3. Raster map of total nitrogen spatial variability
Conclusions
Total nitrogen content in the surface horizon of the investigated field showed small
variability what was confirmed by the low coefficient of variation as well as low value
634
of sill variance. It was caused by differentiated concentration of organic matter in the
field under study.
Geostatistical analysis was confirmed by the micronested structure of total nitrogen
concentration what corroborated with the nugget effect. A significant effect of
autocorrelation between total nitrogen determined for specific sampling points allowed
to increase the distance of soil sampling to 200 m.
References
[1] Gonet S.S. and Dêbska B.: Charakterystyka kwasów huminowych powsta³ych w procesie rozk³adu
resztek roœlinnych. Zesz. Probl. Post. Nauk Roln. 1993, (440), 241–249.
[2] Nowak W. and Sowiñski J.: Zmiany zawartoœci wêgla organicznego, azotu ogólnego i mineralnego
w glebie w czasie wegetacji buraka cukrowego. Zesz. Nauk. AR Szczecin, 1996, (172), 405–412.
[3] Mazur T., Czuba R., Gorlach E., Kalembasa S. and £oginow W.: Azot w glebach uprawnych, PWN,
Warszawa 1999.
[4] Mercik S., Sosulski T. and Rutkowska B,: Chemia rolna, podstawy teoretyczne i praktyczne. Wyd.
SGGW, Warszawa 2002.
[5] Castrignano A., Mazzoncini M. and Giugliarini L.: Spatial characterization of soil properties. Adv.
Geoecol. 1998, 31, 105–111.
[6] Davis J.C.: Statistics and data analysis in geology. John Wiley & Sons, New York 1986.
[7] Spychaj-Fabisiak E. and Murawska B.: Zawartoœæ azotu azotanowego(V) w glebach uprawnych regionu
Pomorza i Kujaw w zale¿noœci od ich w³aœciwoœci fizykochemicznych. Zesz. Probl. Post. Nauk Roln.
2006, 513, 465–471.
[8] D³ugosz J., Spychaj-Fabisiak E., Smoliñski S. and Malczyk P.: Spatial variability of organic carbon and
total nitrogen in the surface horizon of Sepopolska Plain. Humic Substan. Ecosyst. 2005, 6(27), 27–29.
[9] Cambardella C.A., Moorman T.B., Novak J.M., Parkin T.B., Karlen D.L, Turco R.F. and Konopka A.E.:
Field scale variability of soil properties in Central Iowa soils. Soil Sci. Soc. Amer. J. 1994, 58,
1501–1511.
[10] Stenger R., Priesack E. and Beese F.: Spatial variation of nitrate-N and related soil properties at the
plot-scale. Geoderma 2002, 105, 259–275.
[11] Namys³owska-Wilczyñska B.: Geostatystyka. Ofic. Wyd. Polit. Wroc³., Wroc³aw 2006.
ZMIENNOŒÆ PRZESTRZENNA ZAWARTOŒCI AZOTU OGÓ£EM
W POZIOMIE POWIERZCHNIOWYM W SKALI POLA PRODUKCYJNEGO
1
Katedra Chemii Rolnej, 2 Katedra Gleboznawstwa
Uniwersytet Technologiczno-Przyrodniczy w Bydgoszczy
Abstrakt: Azot ogó³em w glebach nie podlega tak du¿ym zmianom w czasie jak jego formy mineralne, ale
jego zawartoœæ mo¿e byæ zró¿nicowana przestrzennie. To zró¿nicowanie mo¿e wystêpowaæ w makroskali np.
regionu, jak i w mikroskali, czyli w obrêbie pola produkcyjnego. Dla praktyki rolniczej szczególnie wa¿ne
jest poznanie zmiennoœci tej formy azotu na obszarze pola, gdy¿ mo¿e to byæ pomocne przy optymalizacji
nawo¿enia. Dlatego te¿ celem niniejszej pracy by³o oszacowanie zmiennoœci przestrzennej azotu ogó³em
w obrêbie pola uprawnego. Do tego celu wytypowano pole po pszenicy ozimej o powierzchni 16,5 ha,
z którego wiosn¹ pobrano próbki z 47 punktów rozmieszczonych co 50 m. Azot ogó³em oznaczono metod¹
Kjeldahla. Na podstawie otrzymanych wyników przy zastosowaniu programu SURFER 8.0 wykreœlono
wariogram empiryczny, który pos³u¿y³ do stworzenia modelu i wykreœlenia mapy rastrowej obrazuj¹cej
rozk³ad badanej formy azotu w obrêbie pola. Wykonano równie¿ obliczenia statystyczne przy u¿yciu
programu STATISTIKA 8.0. Przeprowadzone badanie wykaza³y zró¿nicowan¹ zawartoœæ azotu ogó³em
w poziomie próchnicznym (0,78–1,11 g × kg–1). O niewielkim zró¿nicowaniu analizowanego parametru mo¿e
œwiadczyæ ma³a wartoœæ odchylenia standardowego (0,078) oraz ma³y wspó³czynnik zmiennoœci (8,44 %).
Przeprowadza analiza geostatystyczna wykaza³a, ¿e azot w poziomie powierzchniowym nie wystêpuje
635
w pe³nym rozproszeniu, o czym œwiadczy wystêpowanie efektu samorodka, który dla badanej cechy wynosi³
0,001 (g/kg)2 przy wariancji progowej wynosz¹cej 0,006 (g/kg)2. Du¿y zasiêg wynosz¹cy 212 m œwiadczy
o skorelowaniu zawartoœci azotu ogó³em na odleg³oœci wiêksze ni¿ odleg³oœci miêdzy punktami pobierania
próbek. Dobre dopasowanie modeli (sferycznego i efektu samorodka) potwierdza równie¿ wariancja
obliczona 0,006 (g/kg)2, która jest zbli¿ona do wariancji progowej odczytanej na podstawie tych modeli.
S³owa kluczowe: zmiennoœæ przestrzenna, azot ogó³em, pole produkcyjne, poziom powierzchniowy
A
Vol. 18, No. 4
2011
Alojzy WOJTAS1, Ma³gorzata D¥BEK2,
Gra¿yna PIOTROWSKA3 and Tadeusz MALINOWSKI4
NITROGEN IN WATER FROM WELLS
ZWI¥ZKI AZOTOWE W WODACH STUDZIENNYCH
Abstract: The research, which encompassed the period from 1981 to 2009, was conducted on water samples
collected from 15 wells, 24–103 m in depth, located within the administrative districts of Olecko and Ostroda.
The results of water analyses were varied depending on the location of a well and year of the study. The
waters were characterized by a high content of manganese and iron. Ammonia was found in all the samples
except from the wells in Cimochy, Niemsty, Szczecinki in 2005 and in Gucin in 2009. Nitrate(III) and
nitrate(V) were determined much less frequently than ammonia. None of the three above-mentioned
compounds was detected in three wells in the district of Olecko.
Keywords: groundwater, nitrogen, ammonia, nitrates, water quality
In the region of Warmia and Mazury, potable and other water is drawn from the
quaternary water-bearing floor [1]. Water quality control indicates that most of this
water belongs to Class II. Groundwater from the Quaternary is characterized by an
elevated content of iron and manganese [2]. Sometimes, large amounts of ammonia, in
excess of 1.5 mg N × dm–3, as well as nitrates are found in such water samples [2, 3].
Particularly vulnerable to nitrogen pollution are shallow water-bearing layers near
pastures, animal breeding farms, settlements without sewerage or sewage treatment
plants. The anthropogenic origin of ammonium nitrogen disqualifies most of such
waters from being supplied to water pipeworks [4].
Deep groundwater contains ammonia of the geological origin [3]. Its increased
content is found in waters which flow through layers of brown coal, peat and lignite [5].
Among the characteristics of such water are alkaline reaction and intensive color.
1
Department of Environmental Chemistry, University of Warmia and Mazury in Olsztyn, pl. £ódzki 4,
10–718 Olsztyn, Poland, phone: +48 60 397 37 72, fax: +48 89 523 39 76, email: [email protected]
2
District Health and Epidemiology Centre, Olecko, ul. Wojska Polskiego 13, 19–400 Olecko, Poland.
3
Department of Chemistry, University of Warmia and Mazury in Olsztyn, pl. £ódzki 4, 10–718 Olsztyn,
Poland.
4
Department of Municipal Economy, ul. Zagrodowa 1, 14–105 £ukta, Poland.
638
Alojzy Wojtas et al
Contamination of groundwater may also be the result of its excessive exploitation [4].
Poland belongs to countries with poor water resources. The average annual outflow is
about 1600 m3 per capita, while in some other European countries it reaches 4600 m3
per capita [6]. Therefore, clean water is the greatest wealth of Warmia and Mazury.
The purpose of this study has been to examine tendencies in fluctuations of nitrogen
compounds found in waters from wells in the districts of Ostroda and Olecko.
Some of the physicochemical properties of groundwater sampled from wells in the
districts of Olecko and Ostroda were analyzed (Fig. 1).
DISTRICT OF OSTRODA
DISTRICT OF OLECKO
Fig. 1. Location of water intakes
In accordance with the binding requirements for water sampling, samples of raw
water for laboratory analysis were taken from the following intakes:
Commune
Location, depth of a well [m]
Period
of research
Kowale Oleckie
Wieliczki
Swietajno
Olecko
Lukta
Kowale Oleckie (50), Stozne (77), Szeszki (41)
Cimochy (103), Krupin (62), Niedzwiedzkie (56)
Swietajno (82), Niemsty (83)
Gaski (45), Gordejki Male (67), Lenarty (52), Szczecinki (76), Olecko (63)
Lukta (24), Gucin (40)
1999–2006
1999–2006
2000–2006
1981–2006
2007–2009
Nitrogen in Water from Wells
639
Analyses of water samples were carried out in the Laboratory of Municipal Hygiene
at the District Sanitary and Epidemiological Station in Olecko and at the Sanitary and
Epidemiological Station in Olsztyn. Determination of the physicochemical properties of
water relied on the following methods: pH – by potentiometry, electrolytic conductivity
– by the conductivity method, ammonia – by Nessler’s method, nitrate (III) nitrates (V),
manganese, iron – colorimetrically.
The results were processed using the statistical software packages Statistica and
Excel. Means, standard deviation, regression equations and correlation coefficients were
computed.
Based on the results of our study, which comprised many wells, it was demonstrated
that the quality of drawn water varied, depending on the location of a well and year of
the sampling. The analyzed water samples were characterized by a high content of
manganese and iron (Tables 1, 2). The values of electrolytic conductivity in 13 wells
were on average below 700 mS × cm–1, except the wells in Niemsty (710 mS × cm–1) and
Cimochy (708 mS × cm–1).
Table 1
Szczecinki
Ammonia
mg NH4 × dm–3
Nitrates(III)
mg NO2 × dm–3
Nitrates(V)
mg NO3 × dm–3
Manganese
mg Mn × dm–3
Iron
mg Fe × dm–3
Lenarty
Reaction
pH
Gordejki
Male
Conductivity
mS × cm–1
Gaski
Factors
Location
of wells
Indicators of water quality from wells located in the communes of Olecko and Swietajno
Min.
452
7.3
0.02
0.00
0.10
0.02
0.51
Max
812
7.6
0.39
0.04
11.10
0.11
4.26
X
652
7.5
0.15
0.02
5.52
0.06
1.64
SD
150
0.1
0.14
0.02
5.05
0.04
1.53
Min.
505
7.4
0.37
0.00
0.00
0.08
1.93
Max
535
7.5
0.69
0.00
0.00
0.13
2.77
X
520
7.5
0.53
0.00
0.00
0.10
2.32
SD
15
0.1
0.16
0.02
0.17
Min.
535
7.2
0.41
0.00
0.00
0.06
2.72
Max
577
7.5
0.79
0.00
0.00
0.12
2.81
0.00
0.00
X
556
7.4
0.60
SD
21
0.2
0.19
0.09
2.77
0.03
0.05
Min.
560
7.1
0.00
0.00
Max
642
7.8
0.71
0.02
0.00
0.05
0.70
0.89
0.45
X
593
7.4
0.38
5.18
0.01
0.44
0.17
SD
35
0.3
0.25
3.72
0.01
0.37
0.15
1.57
640
Alojzy Wojtas et al
Gaski
Ammonia
mg NH4 × dm–3
Nitrates(III)
mg NO2 × dm–3
Nitrates(V)
mg NO3 × dm–3
Manganese
mg Mn × dm–3
Iron
mg Fe × dm–3
Niemsty
Reaction
pH
Swietajno
Conductivity
mS × cm–1
Olecko
Factors
Location
of wells
Table 1 contd.
Min.
469
7.0
0.04
0.00
0.00
0.00
0.03
Max
519
8.1
0.39
0.01
1.55
0.14
1.00
X
486
7.7
0.23
0.00
0.41
0.08
0.54
SD
23
0.4
0.11
0.00
0.51
0.05
0.29
Min.
502
7.3
0.15
0.00
0.00
0.06
0.97
Max
547
7.5
0.93
0.03
1.77
0.10
3.23
X
525
7.5
0.39
0.01
0.44
0.08
2.12
SD
23
0.1
0.32
0.01
0.77
0.02
0.83
Min.
683
7.2
0.00
0.00
0.00
0.16
3.24
Max
737
7.3
0.13
0.00
0.00
0.19
4.94
0.00
0.00
X
710
7.3
0.07
SD
27
0.1
0.07
Min.
452
7.3
0.02
0.00
Max
812
7.6
0.39
0.04
X
652
7.5
0.15
0.02
SD
150
0.1
0.14
0.02
0.18
4.09
0.02
0.85
0.10
0.02
0.51
11.10
0.11
4.26
5.52
0.06
1.64
5.05
0.04
1.53
Min. – minimum, Max – maximum, X – average, SD – standard deviation.
Table 2
Stozne
Conductivity
mS × cm–1
Reaction
pH
Ammonia
mg NH4 × dm–3
Nitrates(III)
mg NO2 × dm–3
Nitrates(V)
mg NO3 × dm–3
Manganese
mg Mn × dm–3
Iron
mg Fe × dm–3
Kowale
Oleckie
Factors
Location of wells
Indicators of water quality from wells located in the communes of Kowale Oleckie,
Wieliczki and Lukta
Min.
398
7.4
0.5
0.00
0.00
0.01
2.23
Max
591
7.6
1.46
0.02
0.89
0.23
3.31
X
500
7.5
0.87
0.01
0.22
0.15
2.84
SD
79
0.1
0.36
0.01
0.39
0.09
0.41
Min.
432
7.3
0.15
0.00
0.00
0.06
1.05
Max
489
7.7
0.28
0.04
0.89
0.16
1.69
X
464
7.5
0.23
0.02
0.22
0.11
1.33
SD
24
0.2
0.05
0.02
0.39
0.04
0.26
641
Niedzwiedzkie
Lukta
Gucin
Kowale
Oleckie
Ammonia
mg NH4 × dm–3
Nitrates(III)
mg NO2 × dm–3
Nitrates(V)
mg NO3 × dm–3
Manganese
mg Mn × dm–3
Iron
mg Fe × dm–3
Krupin
Reaction
pH
Cimochy
Conductivity
mS × cm–1
Szeszki
Factors
Location of wells
Table 2 contd.
Min.
524
7.4
0.16
0.00
0.00
0.05
0.95
Max
547
7.8
0.46
0.01
0.89
0.11
2.31
X
534
7.5
0.25
0.00
0.28
0.08
1.56
SD
12
0.2
0.11
0.00
0.36
0.02
0.47
Min.
698
6.7
0.00
0.00
0.00
0.07
3.10
Max
718
7.5
0.59
0.03
0.00
0.23
4.20
X
708
7.1
0.34
0.01
0.00
0.16
3.57
SD
10
0.4
0.21
0.01
0.06
0.44
Min.
520
7.2
0.16
0.00
0.00
0.10
1.16
Max
606
7.5
0.54
0.04
0.66
2.02
2.21
X
557
7.4
0.30
0.02
0.37
0.76
1.85
SD
36
0.1
0.17
0.02
0.27
0.89
0.49
Min.
509
6.9
0.34
0.00
0.00
0.04
1.57
Max
573
7.7
0.94
0.05
44.00
0.19
4.15
X
534
7.5
0.49
0.02
7.60
0.12
2.63
SD
25
0.3
0.21
0.02
16.28
0.05
0.76
Min.
479
6.9
0.03
0.00
0.77
0.03
0.02
Max
634
7.7
0.08
0.01
7.61
0.17
0.38
X
523
7.5
0.05
0.00
4.19
0.10
0.23
SD
44
0.3
0.02
0.00
2.42
0.04
0.11
Min.
526
7.0
0.00
0.00
1.00
0.00
0.00
Max
671
7.7
0.17
0.05
14.60
0.05
0.05
X
629
7.4
0.04
0.01
9.14
0.02
0.01
SD
44
0.2
0.06
0.02
4.14
0.02
0.02
Min.
398
7.4
0.5
0.00
0.00
0.01
2.23
Max
591
7.6
1.46
0.02
0.89
0.23
3.31
X
500
7.5
0.87
0.01
0.22
0.15
2.84
SD
79
0.1
0.36
0.01
0.39
0.09
0.41
Min. – minimum, Max – maximum, X – average, SD – standard deviation.
The water reaction determined in the water samples taken in the districts of Olecko and
Ostroda district fluctuated within the range of 6.7 (Cimochy) to 8.1 (Olecko). The
determined pH did not exceed the standard value assigned to Class I groundwater purity [7].
The standard deviation for these indicators was negligible, ie 10–150 for electrolytic
conductivity and 0.1–0.4 for pH, which confirms the low variability of these
characteristics during the research.
642
Alojzy Wojtas et al
Iron and manganese are among the elements which most often exceeded the set
standards. It was found that these elements appeared in amounts above the threshold
limits for the class I purity water in fourteen of the examined wells, except the one in
Gucin, where, owing to the small amount of manganese (average 0.02 mg Mn × dm–3)
and iron (average 0.01 mg Fe × dm–3), the water was determined to fulfill the criteria for
I class purity [7].
Among the analyzed nitrogen compounds, ammonia nitrogen occurred in all water
samples although its concentration was variable. The standard deviation calculated from
the individual wells ranged from 0.02 to 0.36 in Lukta to 0.36 in Kowale Oleckie. In
water samples from the intakes in Szeszki, Stozne, Niemsty, Gaski, Olecko, Lukta and
Gucin the ammonia content was below 0.5 mg NH4 × dm–3, which corresponds to the
first class of water purity. The other tested water intakes, on at least one occasion,
contained more ammonia, such as water of class II or even class III water purity [7].
Based on the regression equations, it was noticed that the ammonia content during
our study showed an increasing tendency (Table 3). The lowest annual growth rate of
this component was found in the water from the wells in Wieliczki (0.0036 mg
NH4 × dm–3) and Swietajno (0.0038 mg NH4 × dm–3); the highest appeared in the water
from the well in Kowale Oleckie (0.0495 mg NH4 × dm–3). The correlation coefficients
for the results from three communes were negligible, but in the communes of Kowale
Oleckie (r = 0.36) and Olecko (r = 0.38), some weak correlation was determined.
Table 3
Ammonia content of the regression equation (Y) in groundwater depending
on years of research (x) and correlation coefficients (r)
Communities
1
2
3
4
5
Kowale Oleckie
Olecko
Swietajno
Wieliczki
Lukta
Regression equations
Coefficients
of correlation (r)
Y = 0.0495 × x – 98.6395
Y = 0.0121 × x – 23.88675
Y = 0.0038 × x – 7.2926
Y = 0.0036 × x – 6.7397
Y = 0.0100 × x – 20.0233
0.36
0.38
n.s.
n.s.
n.s.
n.s. – non-significant.
Nitrates(III) and (V) appeared much less frequently than ammonia in the analyzed
water samples. In the district of Olecko, nitrates(III) or (V) were not found in just three
wells: Niemsty, Lenarty and Gordejki Male. The concentration of nitrates(V) in the well
in Niedzwiedzkie reached 44.0 mg NO3 × dm–3 in 2005, which corresponds to class III
purity [7]. In the district of Ostroda, the concentration of nitrates(V) in Gucin was only
slightly higher than the standard, by 1.2 mg NO3 × dm–3 in 2007 and 4.6 mg NO3 × dm–3
in 2009.
Conclusions
1. In none of the examined water wells in the district of Ostroda, the concentration of
nitrates (III) exceeded the set standards, while the average concentration of nitrate(V) in
643
the well in Gucin was slightly increased: by 1.2 mg NO3 × dm–3 in 2007 and 4.6 mg
NO3 × dm–3 in 2009. In the district of Olecko, the wells Niemsty, Lenarty and Gordejki
Male contained water free from nitrates(III) and (V).
2. The content of ammonia in groundwater in the commune of Lukta and the wells in
Olecko, Niemsty, Szeszki, Gaski, Stozne was below 0.5 mg NH4 × dm–3 in all years of
the study, ie it remained within the threshold values set for the first class of water
purity, while in the other water samples, it exceeded the upper threshold by 0.04 to 0.96
mg NH4 × dm–3.
3. All the tested water wells located in the districts of Olecko and Ostroda contained
more than standard quantities of iron (an average of 0.04–3.89 Fe mg × dm–3) and
manganese (an average of 0.01–0.71 mg Mn × dm–3), except the well in Gucin, located
in the commune of Lukta.
4. The results of our determinations of pH and electrolytic conductivity showed little
variability in the years of our study, i.e. the pH ranged from 6.7 to 8.1 and the
electrolytic conductivity fluctuated from 398 to 812 mS × cm–1. The average pH values
did not exceed the class I standards established for groundwater, but slightly exceeded
the limits set up for permissible electrolytic conductivity values in the wells in Niemsty
(by 10 mS × cm–1) and Cimochy (by 8 mS × cm–1).
References
[1] Ró¿añski S. (ed.): Raport o stanie œrodowiska województwa warmiñsko-mazurskiego w latach
1999–2000. Biblioteka Monitoringu Œrodowiska, Olsztyn 2001, Czêœæ I – rok 1999, 88–92.
[2] Krajewski Z.W. (ed.): Raport o stanie œrodowiska województwa warmiñsko-mazurskiego w 2003 roku.
Biblioteka Monitoringu Œrodowiska, Olsztyn 2004, 90–94.
[3] Œwiderska-Bró¿ M.: Ochr. Œrodow. 1992, 1(45), 15–20.
[4] Kowal A.L.: Gaz, Woda Techn. Sanit. 2006, 9, 16–20.
[5] £omotowski J. and Haliniak J.: Ochr. Œrodow. 1997, 3(66), 15–17.
[6] Ma³y Rocznik Statystyczny Polski. Zak³ad Wydawnictw Statystycznych, Warszawa 2008.
[7] Rozporz¹dzenie Ministra Œrodowiska z dnia 23 lipca 2008 r. w sprawie kryteriów sposobu oceny stanu
wód podziemnych. DzU nr 143, poz. 896.
ZWI¥ZKI AZOTOWE W WODACH STUDZIENNYCH
1
Katedra Chemii Œrodowiska, Uniwersytet Warmiñsko-Mazurski w Olsztynie
2
Powiatowa Stacja Sanitarno-Epidemiologiczna w Olecku
3
Katedra Chemii, Uniwersytet Warmiñsko-Mazurski w Olsztynie
4
Zak³ad Gospodarki Komunalnej w £ukcie
Abstrakt: Przeprowadzone badania w latach 1981–2009 obejmowa³y wody pobrane z 15 studni po³o¿onych
na terenie powiatu oleckiego i ostródzkiego, których g³êbokoœæ wynosi³a 24–103 m.
Uzyskane wyniki analiz laboratoryjnych wody by³y zró¿nicowane ze wzglêdu na miejsce po³o¿enia studni,
jak i rok badañ. Wody te charakteryzowa³y siê zwiêkszon¹ zawartoœci¹ manganu i ¿elaza. We wszystkich
próbkach, z wyj¹tkiem studni w Cimochach, Niemstach, Szczecinkach w 2005 r. i w Gucinie w 2009 r.,
stwierdzono obecnoœæ amoniaku. Azotany(III) i (V) wystêpowa³y w analizowanych wodach znacznie rzadziej
ni¿ amoniak. W trzech studniach powiatu oleckiego nie odnotowano obecnoœci ¿adnego z tych sk³adników.
S³owa kluczowe: wody podziemne, zwi¹zki azotu, amoniak, azotany, jakoœæ wody
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CHEMICAL SUBSTANCES IN ENVIRONMENT
We have the honour to invite you to take part in the 20th annual Central European
Conference ECOpole ’11, which will be held in 12–15 X 2011 (Thursday–Saturday) at
the Conference Center “Rzemieœlnik” in Zakopane, PL.
The Conference Programme includes oral presentations and posters and will be
divided into five sections:
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The Conference Opening Lecture will be delivered by the Nobel Prize Winner
Professor Dr. Paul Jozef CRUTZEN.
Contributions to the Conference will be published as:
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– extended Abstracts (4–6 pages) in the semi-annual journal Proceedings of ECOpole
– full papers will be published in successive issues of the Ecological Chemistry and
Engineering/Chemia i In¿ynieria Ekologiczna (Ecol. Chem. Eng.) ser. A or S.
Additional information one could find on the Conference website:
ecopole.uni.opole.pl
The deadline for sending the Abstracts is 15.07.2011 and for the Extended Abstracts:
1.10.2011. The actualised list (and the Abstracts) of the Conference contributions
648
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accepted for presentation by the Scientific Board, one can find (starting from
15.07.2011) on the Conference website.
The papers must be prepared according to the Guide for Authors on Submission of
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At the Reception Desk each participant will obtain a CD-ROM with abstracts of the
Conference contributions as well as Conference Programme (the Programme will be
also published on this site).
Further information is available from:
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Chairperson of the Organising Committee
of ECOpole ’11 Conference
University of Opole
and [email protected]
phone +48 77 455 91 49 and +48 77 401 60 42
fax +48 77 401 60 51
Zapraszamy
do udzia³u w Œrodkowoeuropejskiej Konferencji
ECOpole ’11
w dniach 12–15 X 2011
SUBSTANCJE CHEMICZNE
W ŒRODOWISKU PRZYRODNICZYM
Bêdzie to dziewiêtnasta z rzêdu konferencja poœwiêcona badaniom podstawowym
oraz dzia³aniom praktycznym dotycz¹ca ró¿nych aspektów ochrony œrodowiska przyrodniczego. Odbêdzie siê ona w Oœrodku Konferencyjno-Wypoczynkowym „Rzemieœlnik” w Zakopanem.
Doroczne konferencje ECOpole maj¹ charakter miêdzynarodowy i za takie s¹ uznane
przez Ministerstwo Nauki i Szkolnictwa Wy¿szego.
Obrady konferencji ECOpole ’11 bêd¹ zgrupowane w piêciu sekcjach:
– SI Chemiczne substancje w œrodowisku przyrodniczym oraz ich monitoring
– SII Odnawialne Ÿród³a energii i jej oszczêdne pozyskiwanie oraz u¿ytkowanie
– SIII Zarz¹dzanie œrodowiskiem w warunkach kryzysowych
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Pan Profesor Dr Paul Jozef CRUTZEN – Laureat Nagrody Nobla
wyg³osi referat inauguracyjny.
Materia³y konferencyjne bêd¹ opublikowane w postaci:
– abstraktów (0,5 strony formatu A4) na CD-ROM-ie;
– rozszerzonych streszczeñ o objêtoœci 4-6 stron w pó³roczniku Proceedings of
ECOpole;
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strony (wersja cyfrowa + wydruk) planowanych wyst¹pieñ up³ywa w dniu 15 lipca
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bêdzie sukcesywnie publikowana od 15 lipca 2011 r. na stronie webowej
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Aby praca (dotyczy to tak¿e streszczenia, które powinno mieæ tytu³ w jêzyku polskim
i angielskim, s³owa kluczowe w obydwu jêzykach) przedstawiona w czasie konferencji
mog³a byæ opublikowana, jej tekst winien byæ przygotowany zgodnie z wymaganiami stawianymi artyku³om drukowanym w czasopismach Ecological Chemistry and
Engineering ser. A oraz S, które jest dostêpne w wielu bibliotekach naukowych w Polsce i za granic¹. S¹ one takie same dla prac drukowanych w pó³roczniku Chemia – Dydaktyka – Ekologia – Metrologia. Zalecenia te s¹ równie¿ umieszczone na stronie webowej konferencji.
Po konferencji zostan¹ wydane 4–6-stronicowe rozszerzone streszczenia wyst¹pieñ
w pó³roczniku Proceedings of ECOpole. Artyku³y te winny byæ przes³ane do 1 paŸdziernika 2011 r. Wszystkie nadsy³ane prace podlegaj¹ zwyk³ej procedurze recenzyjnej.
Wszystkie streszczenia oraz program Konferencji zostan¹ wydane na CD-ROM-ie, który
otrzyma ka¿dy z uczestników podczas rejestracji. Program bêdzie tak¿e umieszczony na
stronie webowej Konferencji.
Prof. dr hab. Maria Wac³awek
Przewodnicz¹ca Komitetu Organizacyjnego
Konferencji ECOpole ’11
Wszelkie uwagi i zapytania mo¿na kierowaæ na adres:
[email protected]
lub [email protected]
tel. 77 401 60 42 i 77 455 91 49
fax 77 401 60 51
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[3] Bruns I., Sutter K., Neumann D. and Krauss G.-J.: Glutathione accumulation –
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ZALECENIA DOTYCZ¥CE PRZYGOTOWANIA
MANUSKRYPTÓW
Praca przeznaczona do druku w miesiêczniku Ecological Chemistry and Engineering
A/Chemia i In¿ynieria Ekologiczna A powinna byæ przes³ana na adres Redakcji:
Profesor Witold Wac³awek
Redakcja Ecological Chemistry and Engineering
Uniwersytet Opolski
ul. kard. B. Kominka 4, 45–032 Opole
tel. 077 401 60 42, fax 077 401 60 51
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Polecamy symbolikê zalecan¹ przez PTChem (Symbole i terminologia wielkoœci i jednostek stosowanych w chemii fizycznej, Ossolineum, Wroc³aw 1989; Pure Appl. Chem.
1979, 51, 1–41). Materia³ graficzny (rysunki, wykresy), obok wersji na papierze, powinien równie¿ byæ dostarczony w postaci cyfrowych plików wektorowych, np. za pomoc¹ programu: CorelDraw wersja 3.0–8.0, Grafer dla Windows lub przynajmniej bitowe (TIF, PCX, BMP). W przypadku trudnoœci z wype³nieniem tego warunku Redakcja
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Literaturê prosimy zamieszczaæ wg poni¿szych przyk³adów:
[1] Kowalski J. and Malinowski A.: Polish J. Chem. 1990, 40, 2080–2085.
[2] Nowak S.: Chemia nieorganiczna, WNT, Warszawa 1990.
[3] Bruns I., Sutter K., Neumann D. and Krauss G.-J.: Glutathione accumulation –
a specific response of mosses to heavy metal stress, [in:] Sulfur Nutrition and Sulfur
Assimilation in Higher Plants, P. Haupt (ed.), Bern, Switzerland 2000, 389–391.
Tytu³y czasopism nale¿y skracaæ zgodnie z zasadami przyjêtymi przez amerykañsk¹
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zeszytu danego woluminu (w nawiasie, po numerze woluminu).
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REDAKTOR TECHNICZNY
Halina Szczegot
SK£AD I £AMANIE
Jolanta Brodziak
PROJEKT OK£ADKI
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Druk: „Drukarnia Smolarski”, Józef Smolarski, 45–326 Opole, ul. Sandomierska 1. Objêtoœæ: ark. wyd. 13,25,
ark. druk. 10,75. Nak³ad: 350 egz. + 5 nadb. aut.

00a-Tytulowe.vp:CorelVentura 7.0 - Society of Ecological Chemistry

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