INFLUENCE OF DRAINAGE SYSTEMS ON CONTAMINATION WATER AND SOIL
Ivan Šimunić, Franjo Tomić, Lepomir Čoga
Faculty of agriculture University of Zagreb, Croatia, e-mail: simunic@agr.hr
ABSTRACT
This study was aimed: at determining the concentration and leaching of nitrate, atrazine and heavy metals in drainage
water and at determining the concentration of atrazine and heavy metals (Pb, Zn and Cd) in hydroameliorated soil..
The study was conduced on reclamation test field, during of four years. The crop corn was grown. The weed
protection was primextra. Nitrogen fertilization rate was 145 kg.ha-1 to 175 kg.ha-1 Based on the results, it may be
concluded that concentrations of atrazine and NO3 –N in drainage waters exceeded the allowable values (0.1 μg.dm-3)
and (10 μg.dm-3), while the concentrations of heavy metals were below from limited values, like and concentrations
of atrazine and heavy metals in soil.
Since the concentrations of atrazine and NO3 –N in drainage water exceeded the allowable values they need to be
monitored and the actions need to be taken for their reduction.
Key words: reclaimed soil, drainage water, nitrates, atrazine, heavy metals
INTRODUCTION
Different drainage systems with agricultural practices and applications of mineral fertilizers and herbicides may
affect through different pollutants on contamination drainage water and hydroameliorated soil, this is, could
influence on eutrophication of watercourses. In various soil plant systems pollutants may represent a potencial risk to
the environment (Capriel et al. 1985, Mikanová et al. 2001) and uptake by plants and subsequent input into food
chain (Borůvka et al.1996, 1997). The danger ensuing from their tendency to accumulate in vital organs of humans,
animals and plants (bake et al. 1972, Pratt and Jury, 1984, Santa Maria et al. 1986)
Drainage systems and contamination have been the subject of many studies, among which are: Jani and Klaghofer
(1975), Förster (1984), Bocken (1987), Gaynor et al (1989), Milburn and Richards (1994), Webster et al. (1999),
Accinelli et al. (2002) Šimunić at al. (2002a, 2000b and 2002c).
In view of the above facts, this study was aimed
-at determining the concentration and leaching of nitrate, atrazine and heavy metals in drainage water;
-at determining the concentration of atrazine and heavy metals in hydroameliorated soil, since 161 530 ha of
underground drainage systems have been built in Croatia (Marušić, 1995).
2. MATERIAL AND METHODS
Trials were carried out on the experimental amelioration field “Jelenščak”- near Kutina (central Sava valley) on soil
type defined as hydroameliorated Gleyic Podzoluvisol. Trial variants involved pipe drainage spacing of 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 channels. Variants covered areas of: 1425 m 2, 1900
m2, 2375 m2 and 2850 m2. Pipes were plastic (PVC)- annular- ribbed and perforated.
The same crop was grown and the same agricultural practices were applied in all pipe drainage variants in each trial
year (Table 1).
Drainage discharge was measured continually by means of automatic electronic gauges - limnimeters. Limnimeters
were set up in each variant, at the drainpipe outlet into the open canal.
Sampling of drainage water were done three times each month during the discharge period and sampling of soil were
done three times each two months (to atrazine) and each year (to heavy metals).
Nitrates were determined by yellow coloring of phenol disulphonic acid, atrazine was determined by
chromatographic analysis, while heavy metals (Pb, Zn and Cd) by AAS.
The total annual quantity leached of nitrogen, atrazine and heavy metals were estimated on the basis of average
yearly concentration and yearly quantity of drainage discharge.
Data were statistically processed by means of the analysis of variance.
Table 1: Agricultural practices and application terms for maize grown during the period
Year
Sowing
Fertilization
Protection
Harvest
data
Application
date
Quantity
(kg N.ha-1)
Application
date
Quantity
(l.ha-1)
1991
April 30
April 29
July 10
121
54
175
May 2
Oct 20
1993
May 1
April 30
June 18
May 2
1996
May 22
May 20
July 8
May 23
Primextra
(6 l. ha-1)
Nov. 16
1999
May 25
May 23
July 21
94
51
145
97
48
145
101
54
155
Primextra
(6 l. ha-1
=1200 g. ha-1
atrazine)
Primextra
(6 l. ha-1)
May 27
Primextra
(6 l. ha-1)
Oct. 20
Oct 14
3. RESULTS
To facilitate interpretation of research results, the site factors - soil and precipitation - were taken into consideration.
3.1 Soil properties
Drained Gleyic Podzoluvisol is located in the Sava river valley, on level relief (slope<1‰), at an average altitude of
96.4 m a.s.l. Before the trial was set up, the area was utilised as a pasture, which was in association with swamp
vegetation (Salix sp., Juncus sp. etc.).
Genetic texture of the soil profile with major hydropedological indicators is presented in Graph 1, while the major
physical and chemical properties are given in Table 2.
1. Soil type: Gleyic Podzoluvisols, drained, medium deep
2. Main mode of soil moistening: surface and ground water
3. Vertical hydraulic conductivity:
35
35 - 75 cm = 0.011 m/day (very low)
75 - 115 cm = 0.011 m/ day (very low)
75
4. Layering of soil profile:
Ap - Bg - Gso/r - Gr,c
115 5. Depth to impervious horizon, D in m:
ca. 2 m
6. Mean rise of groundwater level, measured from
130
soil surface: ca. 75 cm.
0
Ap
Bg
Gso/r
Gr,c
Figure 1. Genetic texture of Gleyic Podzoluvisol
Table 2: Major properties of drained Gleyic Podzoluvisol
Horizon
Ap
Bt,g
Gso
Gr
Depth
(cm)
0-35
35-75
75-115
115-130
Content of
particles
(%)
Silt
47
45
55
63
Clay
46
48
39
25
Porosity
(%)
%
48
49
46
49
Capacity
(%)
Water
44
45
42
45
Air
4
4
4
4
Permeability Bulk
(m/day)
density
(g.cm-3)
0.011
0.010
0.011
1.35
pH
H2O 1M KCl
6.7
5.3
6.5
5.2
7.9
7.1
Humus
(%)
3.0
The soil has silty clayey texture to the depth of 0.75 m. The clay content of this soil section is in the range of 46-48
%, and the silt content is 45-47 %. The soil depth of 0.75-1.15 m is of lighter texture. The silt component
preponderates in soil texture (55%), while the clay content decreases (39%). Soil texture at depths over 1.15 m is
silty loamy. The soil is porous with the total pore volume of 48-49 %. Soil water capacity is 42-45 %. Air capacity is
low - 4 %. Vertical hydraulic conductivity is very low (0.011 m/day).
3.2 Precipitation characteristics
For the needs of this work, fluctuations of precipitation and drainage discharge have been studied in terms and out of
the growing season.
The four-year precipitation ranged from 897 mm (1996/97) to 1025 mm (1996/97). The primary precipitation
maximum was recorded in the autumn period and the secondary maximum generally in late spring.
Results from Table 3 point to a relatively high precipitation, which had a substantial effect on the particular
pollutants leaching dynamics.
Table 3: Total monthly and annual precipitation and its mean values(mm)
Year V
VI
VII
VIII
IX
X
XI
XII
I
II
III
IV
Σ
1991 156
20
160
52
50
152
108
21
15
45
78
59
916
/92
1993 44
134
30
119
90
107
165
112
50
58
37
79
1025
/94
1996 71
31
90
83
190
46
135
79
44
55
26
45
895
/97
1999 107
89
86
66
95
72
92
104
29
37
63
77
917
/00
3.3 Hydrological relations
Drainage discharge and duration are important indicators of pipe drainage efficiency in draining excess water from
soil. Systems with higher discharge and its shorter duration are more efficient. It would be impossible to estimate the
quantity of leached pollutants in the tested pipe drainage variants without determining the quantity and dynamics of
drainage discharge. Values of the said indicators for different drainpipe spacings are presented in Table 4
Table 4: Quantities of drainage discharge (mm) and total duration drainage discharge (days) per variants
Variant
R 15
R 20
R 25
R 30
R 15
R 20
R 25
R 30
R 15
R 20
R 25
R 30
R 15
R 20
R 25
R 30
Year
Precipitation
(mm)
1991/92
916
1993/94
1025
1996/97
895
1999/00
917
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
Duration of drainage
discharge
(days)
134
136
139
141
167
170
177
182
140
146
153
157
124
126
129
129
Quantity of
drainage discharge
(l/sec)
0.20
0.19
0.18
0.19
0.18
0.18
0.18
0.18
0.16
0.16
0.15
0.15
0.16
0.16
0.15
0.15
It can be seen from Table 4 that there are certain differences in the quantity of drainage discharge, both between the
tested variants in each year and between the trial years. The largest quantities of discharge in all variants were
recorded in the out of the growing season, when evaporation is the lowest, precipitation is the most abundant and
there is no vegetable cover on soil, or plants are in their initial development stage. There are several reasons for these
differences in drainage discharge, primarily the different total annual quantity and distribution of precipitation, as
well as the different efficiency of each particular pipe drainage system. According to Klačić et al. (1998) an average
drainage discharge was 246 mm or 22.5% of total precipitation (1094 mm).
Also there are yearly and seasons differences in the duration of drainage discharge between the tested pipe drainage
systems. Duration of drainage discharge increases with the width of drainpipe spacing and with the quantity of
precipitation and vice versa, narrower spacing and less precipitation cause shorter drainage discharge. We relate the
duration of drainage discharge to the efficiency of each particular pipe drainage system and to all other factors
mentioned for drainage discharge. The foregoing allows the conclusion that narrower drainpipe spacing is more
efficient in these edaphic conditions, which is especially expressed in more humid years. Petošić et al. (1998) report
that the variant involving drainpipe spacing of 10 m rendered the best results in terms of drainage discharge intensity.
3.4. Concentration nitrate nitrogen and leaching in drainage water
Results on the nitrate concentration in drainage water are presented per variants in Table 5.
Table 5: Average and maximum concentration NO3-N (mg.dm-3) in drainage water, per variants
Vari.
1991/92
1993/94
1996/97
1999/00
R 15
R 20
R 25
R 30
Aver
16.25
13.95
15.67
15.26
Max
32.82
30.93
31.67
30.63
Aver
12.90
12.22
12.88
11.95
Max.
29.15
29.03
29.13
29.07
Aver
10.21
10.36
10.58
10.51
Max.
20.05
20.81
20.34
19.91
Aver
9.51
8.99
9.54
9.47
Max
18.15
19.24
20.21
18.43
Maximum concentrations of NO3-N in all variants during the four-year trial period exceeded the concentration of 10
mg.l-1 (Table 5), which is maximal admission concentration of nitrates in water. The highest maximum concentration
for all variants was recorded in 1991/92 and the lowest maximum concentration in 1999/00 .
Average values of NO3-N concentrations (for all variants) only in 1999/00 were below 10 mg.dm-3, while the by far
highest average concentrations was recorded in 1991/92.
It can be seen (Figure 2. pipe drainage spacing of 15 m) that the maximum NO3-N concentrations of all variants in all
years were determined either in the spring or in the summer, soon after sowing and topdressing, which generally
coincided with primary or secondary precipitation (that is, after higher drainage discharge) maxima. Higher
fertilization and higher drainage discharge caused higher concentrations.
The foregoing points to the conclusion that drainage water is exceeded maximal admission concentration of nitrates
in one part of the year (until six monds after second application of fertilization)- (Figure 2 to distance 15 m).
Similar results for drainage water were obtained in a three-year study done by Jani and Klaghofer (1975) in
Petzenkirchen (Lower Austria). They determined an average NO 3-N concentration of 14. 3 mg.l-1. Foerster (1984)
estimated an average concentration of NO 3-N in drainage water of 24.5 mg.l-1 – 38.3 mg.l-1 in northwestern
Germany. Šimunić et al. (2002a) recorded an maximum NO3-N concentration of 28.79 mg/l -32.43 mg/l.
Fluctuation of NO3-N concentracion in drainage water
concentration of NO3-(mg/dm-3)
35
30
25
20
15
10
5
5.
1
7. 99 1
10 199 .
. 1
11 19 9 .
. 1
12 19 9 .
.1 1.
1. 9 91
1 .
2. 99 2
19 .
3. 9 2
1 .
4. 99 2
1 .
5. 99 2
1 .
6. 99 3
1 .
9. 99 3
10 199 .
. 3
11 19 9 .
. 3
12 19 9 .
.1 3.
9
1. 94
19 .
2. 9 4
1 .
3. 99 4
1 .
4. 99 4
1 .
8. 99 4
1 .
9. 99 6
10 199 .
.1 6
11 9 9 .
. 6
12 19 9 .
.1 6.
1. 9 96
1 .
2. 99 7
1 .
3. 99 7
1 .
4. 99 7
1 .
6. 99 7
1 .
9. 99 9
1
10 99 .
. 9
11 19 9 .
. 9
12 19 9 .
.1 9.
1. 9 99
20 .
2. 0 0.
3. 200
2 .
4. 00 0
20 .
00
.
0
years
NO3-N
Figure 2. Fluctuation of NO3-N concentration in drainage water
The total quantity of leached nitrogen and its percentage relative to the total nitrogen added with fertilization are
presented in Table 6.
Table 6:. Quantity of nitrogen leached per pipe drainage variants (kg.ha -1) and percentage of nitrogen leached relative
to the total N added with fertilization
Vari.
1991/92
1993/94
1996/97
1999/00
R 15
R 20
R 25
R 30
Kg.ha-1
35.7
30.7
33.9
34.9
%
20.4
17.5
19.4
19.9
Kg.ha-1
34.4
33.2
34.6
33.2
%
23.7
22.9
23.9
22.9
Kg.ha-1
20.3
20.6
21.5
21.0
%
14.0
14.2
14.8
14.5
Kg.ha-1
16.6
15.8
15.9
16.2
%
10.7
10.2
10.3
10.5
Since the nitrates bind poorly to colloid soil particles, it is important to determine the dynamics of their leaching It
can be seen from Table 6 that the quantity of nitrogen leached varied per years and per trial variants. The lowest
nitrogen leaching was recorded in all variants 1999/00 (the lowest quantity of drainage discharge and lower quantity
of nitrogen added with fertilization). The highest leaching occurred in 1991/92 and 1993/94 (either the highest
nitrogen added with fertilization or was the highest drainage discharge). According to Šoškić et al., (1987) quantity
of nitrogen leached is in linear correlation with the quantity of drainage discharge. The results (Table 6) are in
agreement with the results obtained by Skaggs and Gilliam (1985) and Klačić et al. (1998). Different quantities of
leached nitrogen are conditioned by the climate, namely the quantity 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. Hence, the largest quantities of leached nitrogen were recorded in years with the highest drainage
discharge, this is, with highest precipitation and the highest nitrogen added with fertilization.
It was determined by the analysis of variance that there were no statistically significant differences between the
tested variants of drainpipe spacing in drainage water concentrations of NO 3-N and the quantity of nitrogen leached
in a particular year, at P=0.05 and 0.01.
3.5. Atrazine concentration and leaching in drainage water
Results on atrazine concentration in drainage water and its leaching with drainage water are presented in Tables 7
and 8.
Table 7: Average and maximum concentration atrazine (μg.dm-3) in drainage water, per variants
Vari.
1991/92
1993/94
1996/97
1999/00
Aver
Max
Aver
Max
Aver
Max
Aver
Max
R 15
1.75
7.23
1.55
6.87
0.94
2.88
1.15
5.05
R 20
1.79
7.46
1.71
6.20
0.86
2.32
1.31
5.70
R 25
1.84
7.58
1.89
6.31
0.84
2.95
1.29
5.84
R 30
1.73
7.15
1.57
6.16
0.93
2.99
1.34
5.80
It can be seen from Table 7 that different maximal and average values were determined for atrazine concentrations in
drainage water, both between the trial years and between different drainpipe spacings. This was influenced by the
date of atrazine application, quantity and distribution of rainfall, this is, the quantity of drainage discharge, efficiency
of each particular pipe drainage system. Maximum atrazine concentrations in drainage water were recorded soon
after application and beginning higher drainage discharge (May 1991, Juni 1993, 1999 and Sep. 1996) and in all
years decreased with later drainage discharges (Figure 3 to distance 15 m). Namely, atrazine is very water-soluble
and is readily transported with waters (Albanis et al. 1988) and degraded in soil (Frank et al. 1991b). These results
are in agreement with results, as reported by Ng et al (1995), as well as Accinelli at al. (2002).
In the case of the mentioned atrazine rate (1200 g/ha) applied to the hidroameliorated soil type (Table 2) and the
recorded quantities of precipitation drainage discharge, atrazine concentration were in all years in 10 months higher
from the tolerated limit..Albanis et al. (1988) reported that no atrazine residues were detected in water after 247 days.
Frank et al. (1991b) reported unequal duration of atrazine degradation in soil, from 149 to 684 days, depending on
the temperature and microbiological activity of the soil.
Fluctuation of atrazine concentration in drainage water
concentration of atrazine(ug/dm-3)
8
7
6
5
4
3
2
1
5.
1
7. 991
10 199 .
. 1
11 199 .
. 1
12 199 .
.1 1.
1. 991
1 .
2. 992
1 .
3. 992
1 .
4. 992
1 .
5. 992
1 .
6. 993
1 .
9. 993
10 199 .
. 3
11 199 .
. 3
12 199 .
.1 3.
1. 993
1 .
2. 994
1 .
3. 994
1 .
4. 994
1 .
8. 994
1 .
9. 996
10 199 .
. 6
11 199 .
. 6
12 199 .
.1 6.
1. 996
1 .
2. 997
1 .
3. 997
1 .
4. 997
1 .
6. 997
1 .
9. 999
10 199 .
. 9
11 199 .
. 9
12 199 .
.1 9.
1. 999
2 .
2. 000
2 .
3. 000
2 .
4. 000
20 .
00
.
0
years
atrazine
Figure 3. Fluctuation of atrazine concentration in drainage water
Table 8: Quantity of atrazine leached per pipe drainage variants (g.ha -1) and percentage of leached relative to the
total added with applicatin
Vari
1991/92
g.ha-1
3.99
3.92
3.92
3.96
R 15
R 20
R 25
R 30
1993/94
g.ha-1
4.12
4.63
5.07
4.35
%
0.33
0.33
0.33
0.33
1996/97
g.ha-1
1.86
1.98
1.71
1.85
%
0.34
0.39
0.42
0.36
1999/00
g.ha-1
2.00
2.29
2.14
2.29
%
0.16
0.17
0.14
0.15
%
0.17
0.19
0.18
0.19
Mostly atrazine was lost during the growing season. The larger quantity of total atrazine leached occurred in first two
years (higher total drainage discharge and higher concentrations) and vice verse. Atrazine losses were ranging from
0.14 % to 0.42 %. Frank et al. (1991b) recorded higher values of leached atrazine in drainage water and soil of
predominantly sandy texture (0.2 % to 1.9 % of 3200 active ingredients). Albanis et al. (1988) reported different
quantities of leached atrazine with respect to soil texture (0.54 % in clay, 0.66 % in loam and 0.47 % in silt-loam)
and as Accinelli at al. (2002) reported about 0.61 % atrazine losses in silty loam.
3.6 Atrazine concentration in soil
Atrazine concentration in soil is presented in Table 9, and the dynamics of its concentration in Figure 4.
Table 9. Atrazine concentration in soil (μg.kg-1), per variants
μg.kg-1
Vari
R 15
R 20
R 25
R 30
J
76
77
78
76
A
37
38
37
37
1991/92
O
D
15
7
15
8
16
9
15
7
F
4
4
4
4
A
*
*
*
*
J
59
60
59
59
1993/94
A
O
22
14
23
14
24
15
23
14
D
4
4
5
4
F
*
*
*
*
J
95
93
93
93
A
39
39
40
41
1996/97
O
25
24
25
24
D
16
16
16
15
F
6
6
7
6
A
*
*
*
*
J
105
103
102
102
A
56
55
55
56
1999/00
O
D
37
17
37
17
38
18
35
18
F
6
5
6
5
* Not detected, limit of detection is 2 μg.kg-1
It can be seen from Table 9 that atrazine concentration in soil recorded in the highest values in month Juni, (first
taken of sampling ) and after duration year values are decreased and not detected in April in all years and February
1993/94. Starting concentrations in first two years were recorded lower than in last two years. Maybe was reason
earlier application active ingredient (Table 1), this is, later taken of sampling and earlier drainage discharge (May) in
1991/92 and 1993/94 (a part of atrazine leached and degradeted). According Frank et al. (1991b) soil content of
atrazine is, in fact, the difference between atrazine input into and its output from the soil (losses of residues to water
leaching, disappear by dispersion into air or by degradation) and there are unequal duration of atrazine degradation in
soil, depending on the temperature and microbiological activity of the soil. Half-time dissipation of atrazine in soil
(Figure 4 to distance 15 m) durated until Sept..
A
*
*
*
*
Atrazin in soil and half-time of dissipation
120
HALF-TIME OF DISSIPATION
100
ug/kg
80
60
Series2
40
20
6.
19
99
.
8.
19
99
.
10
.1
99
9.
12
.1
99
9.
2.
20
00
.
6.
19
96
.
9.
19
96
.
10
.1
99
6.
12
.1
99
6.
2.
19
97
.
6.
19
93
.
8.
19
93
.
10
.1
99
3.
12
.1
99
3.
6.
19
91
.
8.
19
91
.
10
.1
99
1.
12
.1
99
1.
2.
19
92
.
0
years
Figure 4. Contents of atrazine in soil and half-time of disspation
The same results are reported by Kozak and Vacek (1996). Frank et al. (1991b) reported half-time of atrazine in soil
from 125 to 198 days. The tolerance limit for atrazine concentration in soil depends on the susceptibility of the next
crop, as well as on the soil physical and chemical properties. Šilješ (1980) for heavy clay soils, gives the following
tolerated atrazine concentrations in soil for the next crop in the crop rotation: oil rape 0.1 ppm (100 g. kg-1) and oats
0.25 ppm.
3.7 Heavy metals in drainage water and their leaching
Results of average concentrations of heavy metals in drainage water and their leaching are presented per year and
per variants in Table 10a, 10b and 10c.
Table 10a. Average yearly concentration of Pb in drainage water (μg.dm-3) and leaching (g.ha-1)
Vari.
R 15
R 20
R 25
R 30
1991/92
μg.dm-3
g.ha-1
28.5
64.98
27.0
59.13
26.0
55.38
27.0
61.83
1993/94
μg.dm-3
g.ha-1
29.0
77.14
28.5
77.24
27.5
73.70
27.5
76.18
1996/97
μg.dm-3
g.ha-1
27.0
53.46
26.5
52.47
27.0
54.81
26.5
52.74
1999/00
μg.dm-3
g.ha-1
24.5
42.63
24.0
42.00
23.5
39.01
24.0
41.04
Table 10b. Average yearly concentration of Zn in drainage water (μg.dm-3) and leaching (g.ha-1)
Vari.
R 15
R 20
R 25
R 30
1991/92
μg.dm-3
g.ha-1
14.9
33.97
14.3
31.32
15.1
32.16
14.5
33.21
1993/94
μg.dm-3
g.ha-1
17.5
46.55
16.7
45.26
16.5
44.22
16.9
46.81
1996/97
μg.dm-3
g.ha-1
15.4
30.42
15.0
29.70
15.1
30.65
14.8
29.45
1999/00
μg.dm-3
g.ha-1
13.9
24.19
14.1
24.68
13.7
22.74
13.8
23.60
Table 10c. Average yearly concentration of Cd in drainage water (μg.dm-3) and leaching (g.ha-1)
Vari.
R 15
R 20
R 25
R 30
1991/92
μg.dm-3
g.ha-1
1.9
4.33
1.7
3.72
1.7
3.62
1.8
4.12
1993/94
μg.dm-3
g.ha-1
2.2
5.85
2.2
5.96
2.2
5.90
2.2
6.09
1996/97
μg.dm-3
g.ha-1
1.7
3.37
1.7
3.37
1.7
3.45
1.7
3.38
1999/00
μg.dm-3
g.ha-1
1.5
2.61
1.5
2.63
1.4
2.32
1.5
2.57
Concentrations of heavy metals in drainage water do not indicate pollution, which is in agreement with the results
obtained by Moore et al. (1981a and 1981b), Đumija et al. (1989) and Čoga et al. (1998). Different average
concentrations of heavy metals were recorded per years and per drainage system variants. The average the highest
concentration of all heavy metals were recorded in 1993/94 when were the highest total drainage discharge. Maximal
concentration duration of all years recorded in the period of higher drainage discharge (Figure 5 to distance 15 m).
Maximal concentration of Pb was from 36.5 μg.dm-3 (1996/97) to 50.5 μg.dm-3 (1991/92), Zn from 20.5 μg.dm-3
(1999/00) to 28.2 μg.dm-3 (1991/92) and Cd
fluctuation of heavy metals(Pb,Zn,Cd) in drainage water
60,00
50,00
ug/dm3
40,00
30,00
20,00
10,00
5.
19
7. 9 1
1 .
10 99
.1 1.
11 9 9
.1 1.
12 9 9
.1 1.
9
1. 91
19 .
2. 9 2
19 .
3. 9 2
19 .
4. 9 2
19 .
5. 9 2
19 .
7. 9 3
1 .
10 99
.1 3.
11 9 9
.1 3.
12 9 9
.1 3.
9
1. 93
19 .
2. 9 4
19 .
3. 9 4
19 .
4. 9 4
19 .
5. 9 4
19 .
7. 9 6
1 .
10 99
.1 6.
11 9 9
.1 6.
12 9 9
.1 6.
9
1. 96
19 .
2. 9 7
19 .
3. 9 7
19 .
4. 9 7
19 .
5. 9 7
19 .
7. 9 9
1 .
10 99
.1 9.
11 9 9
.1 9.
12 9 9
.1 9.
9
1. 99
20 .
2. 0 0
20 .
3. 0 0
20 .
4. 0 0
20 .
00
.
0,00
years
Pb
Zn
Cd
Figure 5. Fluctuation of heavy metals (Pb, Zn and Cd) in drainage water
The recorded concentration of heavy metals and the drainage discharge (Table 4) served to calculate the quantity of
heavy metals leached. The highest leaching were also determined by all heavy metals at the time of its highest
drainage discharge (1993/94), and vice verse. According to Bear and Verryjit (1987), variations in the quantity and
percentage of leached Zn and Cd depend mostly on precipitation, as well as on the quantity and speed of drain water,
which has an appreciable influence on the physical transport of heavy metals.The quantity of leached heavy metals
was smaller than their overall input into soil (Table 11)
The available data point to the conclusion that there are no substantial differences between the tested variants in each
year. Greater differences were recorded between the tested years, which was the effect of the hydrological
conditions, agricultural management procedures applied and air cleanliness.
3.8. Heavy metals in hydroameliorated soil
Table 11. Contents of total heavy metals in soil (mg.kg-1), per variants
Vari
Contets of heavy
Total introduced
metals
g.ha-1
mg.kg-1
1991
During four years
Pb
Zn
Cd
Pb
Zn
Cd
R 15
13.5
77.2
0.7
295.
655.6
55.5
1
R 20
13.5
77.2
0.7
R 25
13.5
77.2
0.7
R 30
13.5
77.2
0.7
Weight of soil (0-0.3 m)= 4050 t.ha-1
It is need 405 g.ha-1 to increasing 0.1 mg.kg-1
Total leaching
g.ha-1
During four years
Pb
Zn
Cd
238.2
135.1
16.2
230.8
131.0
15.7
222.9
129.8
15.3
231.8
133.1
16.2
Difference
(Introduced-leaching)
g.ha-1
Pb
79.7
64.3
72.2
63.3
Zn
520.5
524.6
525.8
522.5
Cd
39.
39.8
40.2
39.3
Contets of heavy
metals
mg.kg-1
2000
Pb
Zn
Cd
13.5
77.2
0.7
13.5
77.2
0.7
13.5
77.2
0.7
13.5
77.2
0.7
The obtained results did not indicate contamination of hydroameliorated soil by heavy metals (Table 11). According
to Mengel and Kirkby (1979), symptoms of toxicity at levels of about 400 mg.kg -1 Zn and higher, Cd levels in
uncontaminated soils do not exceed 1 mg.kg-1 .
Results of content for each metal did not reveal differences within ten-year as well as between the tested variants
within ten-year. For increasing 0.1 mg.kg-1 each heavy metals in soil it is needed 405 g.ha-1 without losses. Šimunić
at al. (2002c) reported that in three-year plants through yield and harvest residues taken out 53.2 g.ha-1 Pb, 399 g.ha-1
Zn and 4.7 g.ha-1 Cd.
The obtained results are relatively lower also in comparison with other studies (Kralovec and Slavík, 1997; Romić
M. and Romić D., 1998), which we attribute to the short time that this soil has been used for agricultural production.
This points to the tentative conclusion that did not have accumulation of heavy metals in hydroameliorated soil..
3.9 Yield of crops
The mean values of crop yields, in dependence on the drainpipe spacing variant, are presented in Table 12.
Table 12: Duncan’s Multiple Range test of the mean values of crop yields (dt.ha -1) in dependence on the drainpipe
spacing variant
Vari.
Dry grain yield (dt.ha-1)
Maize
Maize
Maize
Maize
(1991)
(1993)
(1996)
(1999)
15 m
88.00
a
64.28
a
58.20
a
62.30
a
20 m
81.30
b
63.50
a
53.43
b
61.60
a
25 m
78.66
c
60.80
a
49.15
c
57.70
ab
30 m
71.74
d
60.10
a
43.48
d
56.20
b
Values marked by the same letter are not significantly different according to Duncan’s test (p>0.05)
Yields of the same crops differed in different trial years due to various factors, such as genetic characteristics of the
cultivars, or hybrids, drilling date, total fertilizer applied, topdressing pattern in the growing season, the harvest time
(Table 1), different quantities and distribution of precipitation during the growing season (Table 3). As a rule, the
highest yields were achieved in the drainpipe spacing variant of 15 m, and the lowest in that involving 30 m spacing,
which the authors attribute to the efficiency of particular drainage systems (Tomić et al., 1994 and 2002d; Šimunić,
1995).
Analysis of variance, done separately for each trial year, rendered highly significant differences (p<0.01) between
yields of particular crops in dependence on the drainpipe spacing in all trial years.
Duncan’s test revealed that maize yields were significantly higher in drainpipe spacing variants of 15 m in trial years
1991 and 1996. In 1999 yield was not significantly different between drainpipe variants of 15 m and 20 m.
In 1993 yield was not significantly different between all drainpipe variants. Maybe it was reason in repeated vertical
deep loosening.
Accordingly, satisfactory yields can be achieved with the drainpipe spacing of 15 m. Drainpipe spacing of 20 m,
supplemented by repeated vertical deep loosening, may give satisfactory results in years when the drainage system is
adequately maintained. Hence, drainpipe spacing of 20 m is recommended for Gleyic Podzoluvisol, along with
appropriate and regular maintenance of the drainage system and application of vertical deep loosening of soil (Tomić
et al., 1994; Šimunić, 1995; Petošić et al., 1998).
CONCLUSION
Based on the results, it may be concluded:
1. Concentrations of NO3 –N and atrazine in drainage waters exceeded the allowable values (10 mg.dm-3, 0.1 μg.dm3)
, respectively.
2 .Maximum NO3-N and atrazine concentrations in all variants and in all years were determined either in the spring
or in the summer, soon after sowing and topdressing, which generally coincided with primary or secondary
precipitation (that is, after higher drainage discharge) maxima.
3.Higher applications of fertilization and active ingredients herbicide and higher drainage discharge caused higher
concentrations.
4. Concentrations of atrazine in soil did not detected in April.
5. Concentrations of heavy metals in drainage waters and in soil in all variants and in all years were below from
limited values
6. Contets of heavy metals in soil was the same after ten years.
7. Significant the best yield were on variant of distance 15 m.
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Authors’ address
Prof. Ivan Šimunić, Ph.D.*
Prof. Franjo Tomić, Ph.D.
Lepomir Čoga, Ph.D., Assist. Prof.
Faculty of Agriculture
University of Zagreb
Svetošimunska 25
HR- 10000 Zagreb
*Corresponding author’s e-mail: simunic@agr.hr