LEACHING NITRATE AND ATRAZINE ON THE
RECLAMATION TEST FIELD OF DIFFERENT DRAINPIPE
SPACING
I. SIMUNIC*, F. TOMIC, T. KRICKA
University of Zagreb, Faculty of Agriculture, Svetosimunska 25, 10000 Zagreb,
Croatia
E-mail: simunic@agr.hr
Abstract. The research was conduced on the Jelenščak reclamation test field in Croatia, on
hydroameliorated Gleyic Podzoluvisol during five years. The basic aim of this research is to
determine leaching of nitrate and atrazine in drainage water in four different drainpipe specing (15 m,
20 m, 25 m and 30 m). Maize was grown as the trial crop and the same agricultural practices were
applied in all drainpipe specings in all trial years. Drainage discharge was measured continually by
means of automatic elektronic ganges – limnimeters, which were set up in each variant, at the drainpipe
autlet into the open canal. Drainage water was sampled every day during the discharg period. Nitrates
were determined by the yellow colouring of phenol disulphonic acid: Atrazine extracted from the
samples of drainage waters was determinated by gas chromatography. Data were statistically processed
by means of analysis of variance. Quantity of nitrogen leached were different from year to year and
carrespond to total nitrogen added with fertilization and amont of annual precipitation. The
concentrations of the atrazine recorded in drainage waters varied in a wide range, with maximum
values recorded soon after its application and at the start of higher drainage discharge. The results
indicate that concentrations of nitrate and atrazine drainage waters exceeded the allowable values in the
larger part of the year in all drainpipe spacing. There were no statistically significant differences
between the tested drainage systems in drainage water contamination with nitrate and atrazine.
Keywords: drainage water, maize, leaching, nitrate, atrazine.
AIMS AND BACKGROUND
In various soil-plant systems, pollutants may constitute a potential risk to the
environment through their uptake by plants and subsequent input into the food chain,
and the danger ensuing from their tendency to accumulate in vital organs of humans,
animals and plants, or because of possible contamination of drinking water. The
World Health Organization recommended that drinking water should contain less than
10 mg L-1 NO3-N and 0,100 µg L-1 atrazine1. Pollution of water by nitrates pesticides
is an international problem2-5. Excessive nitrate concentration in water may lead to
eutrophication of watercourses or stock watering. If such water is used for human
consumption, it may cause methemoglobinemia in infants and animals6,7. Potential
cancer risk from nitrate-N (and nitrite) and atrazine in water and food has been
reported 8,9. Leaching of nitrates and atrazine from soil depends on the amount,
frequency and intensity of precipitation, soil properties, crop and crop development
stage, evaporation, soil tillage practices, nitrogen fertilization and application of
herbicide10. The problem of nitrate leaching and atrazine leaching are even more
expressed in agroecosystems of hydroameliorated, especially drained soils because of
changed infiltration and filtration capabilities of these soils. Total hydroameliorated
areas cover 600,054 ha in Croatia, including 117,865 ha of the pipe drainage system
area. Different drainpipe spacing and different nitrogen fertilization and application of
herbicide levels significantly influence soil productivity in the experimental area 11,12,
but different drainpipe spacings with different agricultural practices and application of
mineral fertilizers and herbicide may influence contamination of drainage water 13,14.
1
The main goal of this research was: to determine the quantity of nitrate leaching and
atrazine leaching in drainage water in four different drainpipe spacing.
EXPERIMENTAL
Trials were carried out at the experimental amelioration field located in Jelenscak near
Popovaca, on soil type defined as Gleyic Podzoluvisol. The trial involved four
different drainpipe spacing variants (15 m, 20 m, 25 m and 30 m), set up in four
replications. All variants were combined with gravel as contact material (ø 5-25 mm)
in the drainage ditch above the pipe. Drainpipe characteristics were: length 95 m,
diameter 65 mm, average slope 3‰ and average depth 1 m. Drainpipes discharged
directly into open canals. Variants covered areas of 1425 m2, 1900 m2, 2375 m2 and
2850 m2, respectively. Plastic (PVC)-annular-ribbed and perforated pipes were used.
Maize was grown as the trial crop and the same agricultural practices were applied in
all drainpipe spacing variants during the five trial years (1991, 1993, 1996, 1999 and
2002). Sowing was done in May and harvest took place in October. All measurements
were taken from May to April of the following year because soybean was planted as
the next crop in rotation in May. Total nitrogen fertilization was: 175 kg/ha/year, 145
kg/ha/year, 145 kg/ha/year, 155 kg/ha/year and 164 kg/ha/year. Weed control
involved application of herbicide Primextra 500, based on active substance-atrazine
20%+metolachlor 30%. Drainage discharge was measured continually by means of
automatic electronic gauges-limnimeters, which were set up in each variant at the
drainpipe outlet into the open canal. Drainage water was sampled every day during
the discharge period. Nitrates were determined by the yellow colouring of phenol
disulphonic acid and atrazine by gas chromatography. Total annual quantities of
nitrogen and atrazine leached were estimated on the basis of the average monthly
concentration and monthly quantity of drainage discharge. Data were statistically
processed by means of the analysis of variance (ANOVA).
RESULTS AND DISCUSSION
The trial soil type is found in the Sava river valley at the altitude of 96.4 m a.s.l..
Average groundwater table depth is 1.15 m with strong fluctuations influenced by
precipitation and drainage. Major soil properties are summarized in Table 1.
According to the mechanical composition of the arable layer, the soil is silty clay. Soil
swelling and shrinking properties were determined by the percentage and type of clay
minerals in soil, along with humus content. When dry, the soil has a high proportion
of large blocky aggregates, cracks are large and precipitation can easily percolate
through the soil. When the soil is wet, clay particles swell and water retention is very
low.
Table 1. Major properties of drained Gleyic Podzoluvisol
Profile Depth,
cm
Ap 0-35
Bt,g 35-75
Gso 75-115
Content of Porosity, Capacity, Bulk density, Permeability, pH
particles,
%
%
kg/dm3
m/day
KCl
%
Silt Clay
Water Air
47
46
48
44
4
1.35
0.011
5.3
45
48
49
45
4
0.011
5.2
55
39
46
42
4
0.011
7.1
2
Monthly precipitation values and the corresponding total values (i.e., sum of monthly
precipitation values for the whole examined period) representative of the experimental
station are presented in Table 2. According to analyses of total precipitation values
and total drainage discharge values for different drainpipe spacings (Table 3), it may
be concluded that differences are noticeable in the quantity and duration of drainage
discharge, both between the tested drainpipe spacings in each growing season and
between the trial years. Differences in the quantity of drainage discharge between
drainpipe spacings in a particular year are small, but differences between years are
evident. Correlation coefficients between precipitation and drainage discharge for
different drainpipe spacings during the examined period are shown in Figure 1. It can
be seen that there is strong correlation between precipitation and drainage discharge
and a small difference between drainpipe spacings (r=0.79 up to 0.85). Duration of
drainage discharge in each year increases with the width of drainpipe spacing. On the
basis of ANOVA there are no statistically significant differences between drainage
discharge and duration of drainage discharge at any drainpipe spacing in any trial
year. Narrower drainpipe spacing and shorter duration of drainage discharge are more
efficient15. There may be several reasons for these differences, primarily total
precipitation amounts and their distribution, different efficiency of each particular
drainpipe spacing and agricultural practices applied to maize grown during the trial
period.
Table 2. Monthly precipitation values and the corresponding total values (mm)
Year
1991/92
1993/94
1996/97
1999/00
2002/03
V
156
44
71
107
183
VI
20
134
31
89
56
VII
160
30
90
86
130
VIII
52
119
83
66
99
IX
50
90
190
95
133
X
152
107
46
72
73
XI
108
165
135
92
113
XII
21
112
79
104
54
I
15
50
44
29
71
II
45
58
55
37
21
III
78
37
26
63
5
IV
59
79
45
77
30
Σ
916
1025
895
917
968
3
Table 3. Quantities of drainage discharge (mm) and total duration of drainage
discharge (days)
Drainpipe spacing (m)
15
20
25
30
15
20
25
30
15
20
25
30
15
20
25
30
15
20
25
30
Year
Precipitation (mm)
1991/92
916
1993/94
1025
1996/97
895
1999/00
917
2002/03
968
Drainage discharge
mm
% of precipitation
228
24.9
219
23.9
213
23.3
229
25.0
266
26.0
271
26.4
268
26.1
277
27.0
198
22.1
198
22.1
203
22.7
199
22.2
174
19.0
175
19.1
166
18.1
171
18.6
273
28.2
270
27.9
277
28.6
285
29.4
Correlation between precipitation and drainage discharge
Correlation coefficient
1
0,8
0,6
0,4
0,2
0
15
20
25
30
Drainpipe spacings (m)
Fig. 1. Correlation between precipitation and drainage discharge
Concentration of nitrogen
Maximum nitrogen concentrations in all drainpipe spacing variants during the trial
period exceeded the concentration of 10 mg/L (Table 4). Average values of nitrogen
concentration in four years were in all drainpipe spacing variants above the allowable
concentration, as well as in the year 1999/2000. Higher maximum (and also average)
concentration was recorded in years with higher drainage discharge and higher rates
of nitrogen fertilization (1991/92, 1993/04 and 2002/03).
4
Table 4. Average and maximum concentration of nitrogen (mg.dm-3) in drainage
water
Spacing
variants
(m)
15
20
25
30
1991/92
1993/94
1996/97
1999/00
2002/03
X
Max
X
Max
X
Max
X
Max
X
Max
16.25
13.95
15.67
15.26
32.82
30.93
31.67
30.63
12.90
12.22
12.88
11.95
29.15
29.03
29.13
29.07
10.21
10.36
10.58
10.51
20.05
20.81
20.34
19.91
9.51
8.99
9.54
9.47
18.15
19.24
20.21
18.43
17.37
17.70
17.81
17.82
34.32
33.19
34.71
33.58
It can be seen (Figure 2) for drainpipe spacing of 15 m, that maximum nitrogen
concentrations in all years were determined either in spring or in summer, soon after
sowing and topdressing, which generally coincided with precipitation maxima (i.e.,
after higher drainage discharge). Similar results for nitrogen concentrations in
drainage water were obtained 11,16,17.
The foregoing points to the conclusion that drainage water exceeded the maximum
allowable concentration of nitrates in one part of the year, that is, for up to seven
months.
Fluctuation of NO3-N concentrations in drainage water
35
NO3-N (mg dm-3)
30
25
20
15
10
MDK
1993
1997
1996
2000
2002
Years
april
march
january
february
november
december
september
july
august
may
june
april
march
january
february
november
october
1999
december
june
september
april
march
january
february
december
october
november
april
1994
september
march
august
january
february
december
october
november
september
may
1992
june
april
march
january
1991
february
november
december
july
october
0
may
5
2003
MDK = maximum allowable concentrations
Fig. 2. Fluctuation of nitrogen concentration in drainage water
Leaching of nitrate
According to analyses of total annual quantity of nitrogen leached through drainage
water (Table 5), it may be concluded that differences are certain, both between the
tested drainpipe spacings in each year and between trial years. Differences in the
quantity of nitrogen leached between drainpipe spacings in a particular year are small,
but there are greater differences between years.
Table 5. Quantity of nitrogen leached through drainage water (kg.ha-1) and percentage
of nitrogen leached relative to the total N added with fertilization
Spacing
variants
(m)
15
20
25
30
1991/92
1993/94
1996/97
1999/00
2002/03
Kg/ha
%
Kg/ha
%
Kg/ha
%
Kg/ha
%
Kg/ha
%
35.7
30.7
33.9
34.9
20.4
17.5
19.4
19.9
34.4
33.2
34.6
33.2
23.7
22.9
23.9
22.9
20.3
20.6
21.5
21.0
14.0
14.2
14.8
14.5
16.6
15.8
15.9
16.2
10.7
10.2
10.3
10.5
47.2
48.4
49.4
50.8
28.7
29.5
30.1
31.0
5
Lower nitrogen leaching was recorded in all drainpipe spacing variants in the periods
1996/97 and 1999/00, when the lowest drainage discharge and lower quantity of
nitrogen added with fertilization were recorded. Higher leaching occurred in the years
1991/92, 1993/94 and 2002/03 (either a larger amount of nitrogen added with
fertilization or higher drainage discharge). The quantity of nitrogen leached is in
linear correlation with the quantity of drainage discharge12. Different quantities of
leached nitrogen are influenced by climate conditions, namely the amount and
distribution of precipitation (drainage discharge), crops grown, that is, their
development stages, as well as by the agricultural practices and the time of their
application.
Concentration of atrazine
It can be seen from Table 6 that different maximum and average values were
determined for atrazine concentrations in drainage water, both in trial years and at
different drainpipe spacings. This was influenced by the date of atrazine application,
quantity and distribution of rainfall, that is, the quantity of drainage discharge, and
efficiency of each particular pipe drainage system. Maximum atrazine concentrations
in drainage water were recorded soon after its application and at the start of higher
drainage discharge (May 1991, June 1993, 1999 and September 1996); they decreased
in all years with later drainage discharge. Namely, atrazine is highly water-soluble
and it is readily transported with water and degraded in soil.
Table 6. Average and maximum concentrations of atrazine (μg.dm-3) in drainage
water, per variants
Spacing
variants
(m)
15
20
25
30
1991/92
1993/94
1996/97
1999/00
2002/03
X
Max
X
Max
X
Max
X
Max
X
Max
1.75
1.79
1.84
1.73
7.23
7.46
7.58
7.15
1.55
1.71
1.89
1.57
6.87
6.20
6.31
6.16
0.94
0.86
0.84
0.93
2.88
2.32
2.95
2.99
1.15
1.31
1.29
1.34
5.05
5.70
5.84
5.80
1.91
1.89
1.85
1.87
7.30
7.15
7.22
7.28
It can be seen (Figure 3) for drainpipe spacing of 15 m, that maximum atrazine
concentrations in all years were determined either in spring or in summer, soon after
sowing and topdressing, which generally coincided with precipitation maxima (i.e.,
after higher drainage discharge).
Results on the contamination of drainage water with atrazine, in dependence on
different drainpipe spacing, are in agreement with the results18. These authors point to
the fact that the quantity of atrazine leached in these parts is strongly influenced by
the distribution of precipitation (drainage discharge), time of herbicide application,
their quantities added, and the phenological stage of maize. In the case of the
mentioned atrazine rate (1200 g/ha) applied to hydroameliorated soil and the recorded
quantities of precipitation drainage discharge, atrazine concentrations were higher
than the tolerated limit in 10 months in all years.
6
1991
1994
2000
Years
2002
april
march
january
february
november
december
september
july
august
may
june
april
march
january
february
december
october
1999
november
june
april
1997
september
march
january
february
october
november
1996
december
september
april
august
march
january
february
december
october
1993
november
september
may
1992
june
april
march
january
february
december
july
november
MDK
may
8
7,5
7
6,5
6
5,5
5
4,5
4
3,5
3
2,5
2
1,5
1
0,5
0
october
Atrazine (μg dm-3)
Fluctuation of atrazine concentrations in drainage water
2003
MDK = maximum allowable concentrations
Fig. 3. Fluctuation of atrazine concentration in drainage water
Leaching of atrazine
Table 7. Quantity of atrazine leached through drainage water (g.ha-1) and percentage
of atrazine leached relative to the total quantity added with aplication
Spacing
variants (m)
15
20
25
30
1991/92
-1
g.ha
3.99
3.92
3.92
3.96
%
0.33
0.33
0.33
0.33
1993/94
-1
g.ha
4.12
4.63
5.07
4.35
%
0.34
0.39
0.42
0.36
1996/97
-1
g.ha
1.86
1.98
1.71
1.85
%
0.16
0.17
0.14
0.15
1999/00
-1
g.ha
2.00
2.29
2.14
2.29
%
0.17
0.19
0.18
0.19
2002/03
g.ha-1
5.21
5.10
5.12
5.33
%
0.43
0.43
0.43
0.44
Atrazine was mostly lost during the growing season. Larger quantity of total atrazine
leached was recorded in the first two years (higher total drainage discharge and higher
concentrations) and vice verse. Atrazine losses ranged from 0.14% to 0.44%.
Different quantities of leached atrazine with respect to soil texture (0.54% in clay,
0.66% in loam and 0.47% in silt-loam)19 and about 0.61% atrazine losses in silty loam
18
.
CONCLUSIONS
The foregoing points to the conclusion that drainage water exceeded the maximum
allowable concentration of nitrates in one part of the year, that is, for up to seven
months.
In 10 months in all years and all variants concentrations of atrazine were higher from
the tolerated limit.
Quantity of nitrate and atrazine leached is depended on the total drainage discharge
and its concentrations in drainage water.
ANOVA showed that there were no statistically significant differences between the
tested variants in particular years either in concentrations or in the quantity of leached,
at LSD=0.05.
Acknowledgement. This research was initiated and supported by the Ministry of Science and
Technology of the Republic of Croatia (Project, No. 178131-Systems of Water-Soil-Plant
Management) and the Water Management Agency “Hrvatske vode”, Croatia.
7
REFERENCES
1. WHO: Guidelines for Drinking-water Quality. 2nd Edn. World Health Organization,
Geneva (1998).
2. G. ROBERTS, T. MARSH: The effects of agricultural practices on the nitrate
concentrations in the surface water domestic supply sources of Western Europe.
IAHS, 1987,164: 365-380.
3. F. T. WAKIDA, D.N. LERNER: Nitrate leaching from construction sites to
groundwater in the Nottingham, UK, urban area. Water Sci. Technol., 2002, 45:
243-248.
4. L. SHUKA, I. MALOLLARI, D. VEIZAJ: Assessment of phosphates and nitrates
effects on water quality of the Ohrid and Prespa lakes. Journal of Environmental
and Ecology, 2006, 6, 4:761-770.
5. F. VOSNIAKOS, T. ALAMPANIS, G. VASILIKIOTIS, K.
DIAMANTOPOULOS, E. CHRISTOFORIDOU, A. KARIDA, K. ZAVLARIS, P.
METZELOU, D. LAMPROPOULOU, P. SELIMI, A. KOUGOLOS, K.
VOSNIAKOS, S. AVDIMIOTIS: Evaluation of transboundary pollution levels in
the Axios river (Greece, Former Yugoslavian Republic of Macedonia)-Direct and
indirect impacts on man and environmental. Journal of Environmental and Ecology,
2007, 8, 3:526-534.
6. P. PRATT, W. A. JURY: Pollution of the unsaturated zone with nitrate. Ecol.
Stud., 1984, 47, 52-67.
7. P. A. MATSON, W. J. PARTON, A. G. POWER, M. J. SWIFT: Agricultural
intensification and ecosystem properties. Science 277, 1997, pp. 504–509.
8. P. JASA, S. SKIPTON, D. VARNER, D. HAY: Drinking water: NO3-N.
NebGuide, Published by Cooperative Extension Institute of Agriculture and Natural
Resources. University of Nebraska-Lincoln, 1999.
9. M. JOLÀNKAI, Z. SZENTPÉTERY, Z. HEGEDŰS: Pesticide residue discharge
dynamics in wheat grain. Cereal Research Communications, 2006, 34, 1. 505-508.
10. Z. VIDACEK, M. SRAKA, L. COGA, A. Mihalic: Nitrates, heavy metals and
herbicides in soil and water of Karasica-Vucica catchment area. Agriculturae
Conspectus Scientificus, 1999, 64, 2:143-150.
11. I. SIMUNIC, F. TOMIC, M. MESIC, I. KOLAK: Nitrogen leaching from
Hydroameliorated Soil. Die Bodenkultur, 2002, 53, 2:73:83.
12. M. MESIC, F. BASIC, I. KISIC, A. BUTORAC, I. GASPAR: Influence of
mineral nitrogen fertilization on corn grain yield and nitrogen leaching. Cereal
Research Communications, 2007, 35, 2:773-776.
13. P. MILBURN, J.E. RICHARDS: Nitrate concentration of the subsurface drainage
water from a corn field in southern New Brunswick. Canadian Agricultural
Engineering, 1994, 36, 2: 69-78.
14. C. WEBSTER, P. R. POULTON, K. W. T. GOULDING: Nitrogen leaching from
winter cereals grown as part of a 5-yearly-arable rotation. European Journal of
Agronomy, 1999, 10: 99-109.
15. F. TOMIC, I. SIMUNIC, D. PETOSIC, D. ROMIC, Z. SATOVIC: Effect of
drainpipe spacing on the yield of field crops grown on hydroameliorated soil.
Agriculturae Conspectus Scientificus, 2002, 67, 2:101-105.
16. E. J. KLADIVKO, J. R. FRANKENBERGER, D. B. JAYNES, D. W. MEEK, B.
J. JENKINSON, N. R. FAUSEY: Nitrate leaching to subsurface drains as affected
by drain spacing and changes in crop production system. Journal of
Environmental Quality, 1991, 20, 1: 264-270.
8
17. N. ROSSI, C. CIAVATTA, L.V. ANTISARI: Seasonal pattern of nitrate losses
from cultivated soil with subsurface drainage. Water, Air and Soil Pollution, 1991,
60, 1-2: 1-10.
18. C. ACCINELI, A. VICARI, P. ROSSI, P. CATIZONE: Losses of atrazine,
metolachlor, prosulfuron and triasulfuron in subsurface drain water. Agronomie,
2002, 22: 399-411.
19. T. A. ALBANIS, P. J. OMONIS, A. T. SDOUKOS: Movement of methyl
parathion, lindane and atrazine through lysimeters in field conditions.
Toxicological and Environmental Chemistry, 1998, 17: 35-45.
9