106 TOMASZ SOSULSKI, EWA SZARA, MARIAN KORC, WOJCIECH STÊPIEÑ
http://www.degruyter.com/view/j/ssa (Read content)
SOIL SCIENCE ANNUAL
Vol. 64 No 3/2013: 106113
*email: tomasz_sosulski@sggw.pl
DOI: 10.2478/ssa-2013-0017
INTRODUCTION
In recent years, Europe has seen weather events leading to intense infiltration of the soil profile by rainwater (Westra et al., 2013). Although it is diffi-cult to determine definitely whether the climatic con-ditions on our continent are being or have been fun-damentally altered, meteorological observations ne-vertheless confirm the occurrence of weather anoma-lies seen so far on a much smaller scale. In assessing them, it should be remembered, however, that not so long ago in Poland emphasis was given to the possi-bility of the so-called steppization (turning into step-pes) of agricultural areas. More recently, attention has been drawn to the process of global warming, which in Poland is to produce effects such as increased amo-unts of precipitation. Although the total annual pre-cipitation recorded in central Poland does not differ from the multi-year average, we have recently been dealing with a noticeable increase in the intensity and number of single precipitation events. More impor-tantly, the heavy precipitation events are preceded by longer periods of drought. Such a situation has a
fun-damental impact on the intensity of infiltration of the soil profile by rainwater and promotes intensive sur-face runoff and soil erosion. In the literature, the pre-vailing view so far has been that the outflow of nu-trients from fields takes place mostly outside of the growing season (Misztal and Smal, 1991). However, the volume and lengthy duration of the precipitation events that have occurred in recent years during the growing season make us believe that intense leaching of components from the soil can also occur during the vegetation period, and that the protracted droughts in autumn can markedly inhibit the leaching of com-ponents outside of the growing season.
The Department of Agricultural Chemistry of Warsaw University of Life Sciences SGGW is in charge of long-term fertilization experiments located in Skierniewice. These experiments have been con-ducted in an unchanging way since the early 1920s. In 2011, drainage systems were installed on selected plots of these long-term fertilization experiments to measure the extent of the outflow of mineral elements from the soil under different fertilization and crop production systems. The aim of this study was to as-TOMASZ SOSULSKI*, EWA SZARA, MARIAN KORC, WOJCIECH STÊPIEÑ
Warsaw University of Life Science, Department of Soil Environment Sciences Nowoursynowska 159, building no. 37, 02-776 Warszawa
Leaching of macronutrients, micronutrients and aluminium
from the soil under long-term fertilizer experiments in Skierniewice
(Central Poland)
Abstract: The aim of the study was to determine the levels of soil mineral elements in groundwater and the volume of that water draining from fields under different fertilization systems. In 2011, drainage systems were installed to collect groundwater from selected plots of long-term fertilization experiments located at the Experimental Station of the Faculty of Agriculture and Biology of Warsaw University of Life Sciences SGGW in Skierniewice. The study involved limed (CaNPK) and unlimed (NPK) plots of two fertilization experiments, one with mineral and the other with mineral-organic fertilization. During the study, the volume of the drainage water was measured and samples of the water were analyzed for Ca, Mg, K, Na, Zn, Fe, Mn, Cu and Al. The levels of mineral elements in the water flowing out of the soil profile were found to vary significantly and were dependent on the volume of the outflow, the system of fertilization and soil acidification. The load of elements in the outflow water can be put in the following relative order: Ca>Mg>K>Na>Al>Zn>Fe>Mn>Cu. Application of manure in the dose of fertilizers increased the leaching of ma-gnesium and potassium, as well as zinc, iron and manganese. However, organic fertilization did not increase the leaching of calcium from the soil, and reduced the activity and mobility of aluminium in the soil. Depending on the fertilization system and soil acidifi-cation status, the amounts of elements washed out with 1 m3 of water flowing out of ha a sandy soil were: 186434 g Ca, 12.633 g Mg, 13.280 g K, 9.323.4 g Na, 29.5251 mg Al, 53184 mg Zn, 24.5319 mg Fe, and 2076.5 mg Mn.
sess the amounts of soil minerals in the drained gro-undwater and the extent of their outflow from the fields under two fertilization schemes: mineral and mineral-organic.
MATERIALS AND METHODS
In May 2011, drainage systems were installed to collect groundwater from selected plots of long-term fertilization experiments located at the Experimental Station of the Faculty of Agriculture and Biology of Warsaw University of Life Sciences in Skierniewice. Each drainage system consists of a perforated PVC drainage pipe 100 mm in diameter, coated with syn-thetic fibres, laid in a PVC U-profile in the soil at a depth of 120 cm. The length of the drainage pipe al-lows the drained water to be collected over the entire length of the plot. The drained groundwater is collec-ted into graduacollec-ted vessels placed in inspection cham-bers. Because the installation of the drainage systems involved a major intrusion into the soil environment of the experimental fields maintained since 1922, it was decided that the systems would be installed on one of three replicate plots of the selected experimen-tal combination in field A with arbitrary crop rota-tion without legumes and not fertilized with manure, and on one of five replicate plots in field E with a five-field crop rotation with a leguminous plant (po-tatoes + 30 t manure·ha1, barley, yellow lupin,
win-ter wheat, rye). In pursuing the objective of the stu-dy, the drainage systems were installed on those plots of the long-term fertilization experiments which were part of a fertilization scheme involving mineral ferti-lization only and combined mineral-organic fertili-zation (Tab. 1). In the first year of the study (2011), samples of the groundwater from all the plots were collected in the last year before liming. Samples col-lected in 2012 represented the conditions existing in the soil soon after liming. Triticale was grown in field A in 2011 and mustard in 2012; in field E potatoes and barley, respectively.
In 2011, volume measurements and sampling of the drained groundwater in the inspection chambers
were performed at weekly intervals from mid-May until the first subzero temperatures in November; during periods of intense rainfall, however, the gro-undwater was collected every 23 days. In the winter of 2011/2012, monitoring and sampling of the dra-inage water was performed during periods of thaw. In 2012, in turn, the measurements of the volume of the drained groundwater and collection of samples were performed from after the last frost at the begin-ning of March until the first subzero temperatures in November at 7-day intervals, like in 2011, increasing the frequency of these tasks during periods of heavy rainfall. The monitoring of the outflow and sampling of the drained groundwater in 2012 was completed in the last week of the year. The total number of wa-ter samples analyzed was 92: 36 samples in 2011 year (9 terms from 4 fertilization objectives of the study) and 56 samples in 2012 (14 terms from 4 fertiliza-tion objectives of the study)
The collected water samples were analyzed to determine the levels of macroelements: calcium, ma-gnesium, potassium and sodium, and microelements: zinc, iron, manganese and copper. The samples were additionally analyzed for aluminium content. The amounts of all the elements were determined by ato-mic absorption spectrometry in the laboratory of the Department of Agricultural Chemistry, Warsaw Uni-versity of Life Sciences, in Warsaw, using an M6 Solar Thermo Elemental apparatus. The data were stati-stically analyzed to determine the element concen-trations variability in the groundwater using SPSS Statistic 21.
RESULTS AND DISCUSSION
The amounts of mineral elements in the water moving through the soil profile on the experimental plots selected for the study showed considerable va-riation between successive test dates in 20112012 years (Tab. 2 and 3). Evidenced by the relatively high value of the calculated statistics: standard deviation (SD) and coefficient of variation (V%) in individual years of the study (Tab. 2 and 3). This is a characteri-stic feature of the groundwater flo-wing out of the soil, as described by many researchers concerned with this subject (Baran et al., 2011; Pulikowski et al., 2007; Igras, 2004; Ruszkowska et al., 1999; Steele et al., 1984). Statistical analysis of the data showed that the distribution of the concentrations of Ca, Mg, K, Na, Fe, Zn, Mn, Al in water flowing out of the soil selected for research n o it a zi li tr e F m e t s y s Ef(xeiplde)irment Croprotaiton mFeantrulirzieaiton mineral l a r e n i M A arbirtaryrotaiton s e m u g el t u o h ti w none CNaPNKP*K* ci n a g r o -l a r e n i M E ifve-feildrotaiton ,y el r a b ,s e o t a t o p ( ) e y r ,t a e h w , n i p u l a h t 0 3 1every s r a e y e v if CNaPNKP*K*
Explanation: *CaNPK, NPK: 90 kg N·ha1as ammonium nitrate, 26 kg P·ha1 as single
super-phosphate and 91 kg K·ha1 as potassium chloride, 1,5 t CaO· ha1 every 4 years. TABLE 1. Scheme of experiments
108 TOMASZ SOSULSKI, EWA SZARA, MARIAN KORC, WOJCIECH STÊPIEÑ r a e Y Feild Fetrliziaiton Value Ca Mg K Na e r u n a m mineral mg·dm3 1 1 0 2 A none CaNPK min-max e g a r e v a * % V ; D S 0 0 . 4 0 1 -7 3 . 5 5 5 . 1 8 0 . 5 2 ; 3 3 . 0 2 0 8 . 0 1 -4 7 . 3 1 0 . 9 0 . 2 2 ; 6 0 . 2 5 9 . 2 -7 8 . 1 8 5 . 2 0 . 6 1 ; 2 4 . 0 6 2 . 8 -7 2 . 5 7 9 . 5 0 . 6 1 ; 4 9 . 0 K P N min-max e g a r e v a * % V ; D S 1 2 . 6 8 -4 7 . 8 1 7 0 . 7 6 0 . 1 3 ; 2 6 . 0 2 9 7 . 4 1 -8 8 . 9 9 9 . 1 1 0 . 4 1 ; 4 8 . 6 1 5 0 . 5 -6 5 . 1 5 3 . 3 0 . 8 3 ; 7 2 . 1 4 1 . 4 1 -4 1 . 5 5 6 . 9 0 . 6 3 ; 9 3 . 3 E 30 ·tha1 CaNPK min-max e g a r e v a * % V ; D S 9 2 . 8 0 3 -2 2 . 3 4 6 3 . 0 0 2 0 . 1 3 ; 4 2 . 1 6 8 0 . 6 2 -7 6 . 4 1 6 7 . 9 1 0 . 6 1 ; 4 2 . 3 6 9 . 3 1 -5 1 . 3 2 9 . 7 0 . 7 4 ; 5 7 . 3 1 8 . 7 2 -6 0 . 5 6 2 . 3 1 0 . 6 4 ; 4 0 . 6 K P N min-max e g a r e v a * % V ; D S 7 3 . 7 7 2 -9 3 . 4 9 5 9 . 2 6 1 0 . 1 3 ; 8 0 . 0 5 6 6 . 1 3 -2 9 . 9 1 7 3 . 5 2 0 . 7 1 ; 6 3 . 4 7 3 . 4 2 -5 8 . 2 6 2 . 9 0 . 9 8 ; 5 2 . 8 3 3 . 0 2 -6 5 . 1 1 4 3 . 4 1 0 . 9 1 ; 8 7 . 2 2 1 0 2 A none CaNPK min-max e g a r e v a * % V ; D S 8 9 . 2 1 1 -8 8 . 9 1 5 5 . 1 8 5 . 0 4 ; 3 0 . 3 3 0 0 . 2 2 -0 3 . 6 0 4 . 5 1 0 . 9 3 ; 0 1 . 6 5 2 . 3 1 -6 4 . 0 7 5 . 4 0 . 2 0 1 ; 7 6 . 4 1 1 . 3 -1 2 . 0 3 4 . 1 0 . 0 7 ; 1 0 . 1 K P N min-max e g a r e v a * % V ; D S 7 8 . 4 8 -6 5 . 2 1 8 4 . 3 5 2 . 1 5 ; 8 3 . 7 2 0 8 . 5 2 -0 8 . 2 0 8 . 8 1 0 . 9 3 ; 0 3 . 7 0 0 . 0 1 -8 9 . 1 6 4 . 4 0 . 9 4 ; 8 1 . 2 9 9 . 3 -2 1 . 0 8 6 . 1 0 . 0 8 ; 5 3 . 1 E 30 ·tha1 CaNPK min-max e g a r e v a * % V ; D S 0 6 . 1 1 1 -2 3 . 6 4 3 . 4 5 1 . 9 6 ; 5 5 . 7 3 0 2 . 5 2 -0 7 . 2 0 2 . 4 1 0 . 9 4 ; 0 0 . 7 3 5 . 2 4 -4 4 . 1 9 0 . 1 1 0 . 9 6 ; 7 2 . 3 1 4 1 . 5 -1 2 . 0 8 0 . 2 0 . 9 4 ; 5 8 . 1 K P N min-max e g a r e v a * % V ; D S 2 1 . 0 9 -6 1 . 8 0 0 . 7 4 7 . 8 7 ; 8 9 . 6 3 0 1 . 6 2 -0 1 . 5 0 2 . 5 1 0 . 0 5 ; 0 6 . 7 7 4 . 4 4 -4 3 . 2 2 3 . 4 1 0 . 7 8 ; 7 5 . 2 1 4 1 . 5 -5 4 . 0 4 8 . 1 0 . 5 8 ; 7 5 . 1 e g a r e v A A none CaNPK average 81.6 5.3 3.6 3.7 K P N 60.3 6.9 3.9 5.7 E 30 ·tha1 CaNPK 127.4 10.6 9.5 7.7 K P N 105.0 13.4 11.8 8.1
TABLE 2. Effect of fertilization and crop rotation on the amounts of Ca, Mg, K and Na (mg·dm3) in the water infiltrating the soil
profile to a depth of 120 cm r a e Y Feild Fetrliziaiton Value Zn Fe Mn Al e r u n a m mineral µg·dm3 1 1 0 2 A none CaNPK min-max e g a r e v a * % V ; D S 3 . 7 4 -0 . 6 < 9 . 0 1 5 3 1 ; 8 . 4 1 3 . 2 3 -6 . 3 < 3 . 5 1 6 ; 3 . 3 0 . 6 -8 . 1 < 0 . 5 7 6 ; 4 . 3 7 . 8 4 1 -3 . 4 5 2 . 1 8 6 ; 7 . 4 K P N min-max e g a r e v a * % V ; D S 5 . 9 0 1 -0 . 6 < 6 . 2 1 4 1 ; 6 . 8 1 0 . 6 5 -6 . 3 < 2 . 4 1 4 6 ; 3 . 2 2 8 . 3 1 -8 . 1 < 3 . 6 4 5 ; 4 . 3 2 . 2 2 1 -7 . 9 7 8 . 6 0 1 2 1 ; 7 0 . 3 1 E 30 ·tha1 CaNPK min-max e g a r e v a * % V ; D S 9 . 2 6 -0 . 6 < 2 . 4 1 1 4 1 ; 0 . 0 2 0 . 9 6 -6 . 3 < 6 . 7 2 8 ; 2 . 6 4 8 . 1 1 -8 . 1 < 3 . 6 1 5 ; 2 . 3 0 . 1 4 -0 . 6 < 1 . 0 2 5 3 ; 1 . 7 K P N min-max e g a r e v a * % V ; D S 0 . 4 1 1 -0 . 6 < 3 . 0 3 9 1 1 ; 0 . 6 3 9 . 7 6 -6 . 3 < 2 . 3 3 9 3 ; 2 . 3 1 7 . 4 6 -8 . 1 < 1 . 1 1 5 8 1 ; 6 . 0 2 0 . 1 0 1 -0 . 6 < 5 . 3 2 6 1 ; 7 . 3 2 1 0 2 A none CaNPK min-max e g a r e v a * % V ; D S 4 . 3 6 -0 . 6 < 1 9 . 7 1 6 9 ; 2 . 7 5 . 5 3 -6 . 3 < 2 . 8 6 4 1 ; 0 . 2 1 4 . 5 3 -8 . 1 < 4 . 6 5 6 1 ; 6 . 0 1 1 . 4 4 1 -0 . 6 < 0 . 5 5 0 8 ; 8 . 3 4 K P N min-max e g a r e v a * % V ; D S 5 . 7 7 -0 . 6 < 1 . 2 2 5 0 1 ; 4 . 0 2 3 . 8 6 -6 . 3 < 0 . 9 2 0 2 ; 3 . 8 1 3 . 3 4 -8 . 1 < 2 . 7 8 5 1 ; 4 . 1 1 1 . 9 0 3 -0 . 6 < 5 . 4 0 1 4 7 ; 9 . 6 7 E 30 ·tha1 CaNPK min-max ; D S e g a r e v a * % V 8 . 4 5 -0 . 6 < 5 . 2 2 7 2 1 ; 6 . 8 2 8 . 5 7 1 -6 . 3 < 4 . 2 2 8 0 2 ; 7 . 6 4 8 . 0 7 -8 . 1 < 2 . 3 1 1 6 1 ; 3 . 1 2 7 . 8 9 3 -0 . 6 < 8 . 5 4 4 2 ; 1 . 1 1 K P N min-max e g a r e v a * % V ; D S 4 . 3 6 -5 . 9 2 . 1 3 2 6 ; 4 . 9 1 7 . 3 4 2 -6 . 3 < 2 . 8 5 3 2 1 ; 2 7 2 . 7 2 -8 . 1 < 3 . 3 1 6 7 ; 2 . 0 1 9 . 6 0 6 -0 . 6 < 0 . 7 4 1 3 ; 5 . 4 1 e g a r e v A A none CaNPK average 14.4 6.8 5.7 68.1 K P N 17.4 11.6 6.8 105.7 E 30 ·tha1 CaNPK 18.4 15.0 9.7 34.6 K P N 30.8 45.7 12.2 33.5
Explanation: *SD standard deviation, V% coefficient of variation.
TABLE 3. Effect of fertilization and crop rotation on the amounts of Zn, Fe, Mn, Al (µg·dm3) in the water infiltrating the soil profile
to a depth of 120 cm
109
Leaching of elements from soil under long-term fertilization
r a e Y Feild Manure Mineral Parameters n o it u b it si d f o Ca Mg K Na Fe Zn Mn Al 1 1 0 2 A CaNPK Medain s s e n w e k s a z o tr u K 4 6 3 . 3 8 5 0 1 . 0 -2 8 1 . 2 -5 6 5 . 9 8 1 4 . 0 -* 2 0 8 . 3 1 9 6 . 2 6 0 7 . 0 -2 2 8 . 0 -6 0 0 . 6 * 3 4 4 . 2 * 6 9 1 . 6 0 0 6 . 3 * 6 2 8 . 2 * 2 0 3 . 8 2 0 1 . 7 * 9 1 9 . 1 * 0 9 8 . 3 6 5 9 . 5 * 7 1 4 . 2 -* 4 2 1 . 6 5 3 1 . 6 7 5 8 1 . 2 * 5 0 6 . 5 K P N Medaina s s e n w e k s a z o tr u K 1 6 4 . 8 6 * 5 2 8 . 1 * 8 3 4 . 4 0 9 3 . 1 1 6 0 5 . 0 -8 4 9 . 0 -2 9 2 . 3 5 5 0 . 0 1 4 3 . 1 -6 8 6 . 8 4 9 2 . 0 4 2 5 . 1 -3 4 0 . 4 * 6 6 5 . 1 9 2 9 . 0 0 0 0 . 6 * 6 7 0 . 3 * 7 7 5 . 9 4 7 . 6 5 2 2 . 0 8 0 4 . 0 -5 3 4 . 0 1 1 6 6 9 . 0 -6 7 5 . 0 E 30 ·tha1 CaNPK Medain s s e n w e k s a z o tr u K 6 4 . 7 8 1 5 4 6 . 0 8 2 7 . 0 -8 9 5 . 8 1 7 1 6 . 0 4 2 1 . 1 6 8 8 . 6 8 5 2 . 0 8 2 2 . 1 -1 9 1 . 2 1 * 3 2 8 . 1 * 3 3 . 5 0 0 6 . 3 * 1 5 9 . 2 * 4 7 7 . 8 0 0 2 . 7 * 9 3 1 . 2 * 0 3 1 . 5 0 9 0 . 8 8 5 2 . 0 -2 5 5 . 1 -9 7 3 . 6 0 4 3 . 0 5 2 1 . 2 K P N Medain s s e n w e k s a z o tr u K 7 4 6 . 3 5 1 8 6 4 . 1 * 5 1 7 . 3 8 5 2 . 4 2 8 0 6 . 0 2 5 8 . 0 -2 4 9 . 4 8 9 2 . 1 2 1 1 . 0 1 8 0 . 4 1 2 9 3 . 1 0 9 8 . 1 3 9 2 . 4 3 7 5 0 . 0 5 2 8 . 1 -4 3 . 6 2 * 5 1 9 . 1 * 4 1 5 . 4 3 8 9 . 5 * 4 7 7 . 2 * 9 9 9 . 7 0 0 0 . 6 6 2 5 . 1 0 6 2 . 1 2 1 0 2 A none CaNPK Medain s s e n w e k s a z o tr u K 9 7 3 . 3 8 5 0 1 . 0 -* 2 8 1 . 2 7 8 . 4 1 8 1 4 . 0 -* 2 6 8 . 3 0 7 1 . 6 8 0 7 . 0 -2 2 8 . 0 -1 5 0 . 1 8 3 4 4 . 2 * 6 9 1 . 6 3 2 4 9 . 0 * 6 2 8 . 2 * 2 0 3 . 8 5 5 7 . 4 1 * 9 1 9 . 1 * 4 2 1 . 6 6 1 . 3 * 7 1 4 . 2 -* 4 2 1 . 6 9 2 5 . 4 4 * 5 8 1 . 2 * 5 0 6 . 5 K P N Medain s s e n w e k s a z o tr u K 7 8 . 6 5 5 2 8 . 1 -* 8 3 4 . 4 8 2 8 . 0 2 6 0 5 . 0 8 4 9 . 0 -6 3 9 . 3 5 5 0 . 0 * 0 4 3 . 1 -2 6 5 . 1 4 9 2 . 0 4 2 5 . 1 -6 1 2 . 1 * 6 6 5 . 1 0 2 9 . 0 8 4 9 . 2 1 * 6 7 0 . 3 * 7 7 5 . 9 7 3 4 . 4 * 5 2 2 . 0 * 8 0 4 . 0 -5 3 4 . 2 0 1 6 6 9 . 0 -6 7 5 . 0 E 30 ·tha1 CaNPK Medain s s e n w e k s a z o tr u K 5 2 9 . 4 6 5 4 6 . 0 8 2 7 . 0 -3 3 . 3 1 7 1 6 . 0 4 2 1 . 1 6 3 7 . 6 * 8 5 2 . 0 8 2 2 . 1 -1 5 8 . 0 * 3 2 8 . 1 * 3 3 3 . 5 0 5 0 . 0 * 1 5 9 . 2 * 4 7 7 . 8 5 9 4 . 0 2 * 9 3 1 . 2 * 0 3 1 . 5 0 0 7 . 6 8 5 2 . 0 -2 5 5 . 1 -0 9 5 . 3 0 4 3 . 0 -* 5 2 1 . 2 K P N Medain s s e n w e k s a z o tr u K 5 4 7 . 6 4 8 6 4 . 1 5 1 7 . 3 5 0 7 . 4 1 8 0 6 . 0 2 5 8 . 0 -1 2 7 . 6 * 8 9 2 . 1 2 1 1 . 0 9 2 9 . 0 * 2 9 3 . 1 0 9 8 . 1 1 1 8 . 8 2 7 5 0 . 0 * 5 2 8 . 1 5 4 3 . 4 2 * 6 1 9 . 1 * 4 1 5 . 4 1 1 3 . 2 1 * 4 7 7 . 2 * 0 9 9 . 7 0 0 8 . 5 * 8 2 5 . 1 * 0 6 2 . 1 -1 1 0 2 2 1 0 2 A none CaNPK sMkeewdnaienss a z o tr u K 8 2 3 . 3 8 6 9 8 . 0 -7 0 9 . 0 -7 4 4 . 0 1 * 0 2 0 . 1 6 2 1 . 1 0 5 9 . 3 * 6 9 0 . 1 1 1 2 . 0 -6 7 8 . 2 * 7 3 1 . 1 * 2 0 6 . 1 0 0 6 . 3 * 8 2 7 . 1 4 0 7 . 1 4 7 6 . 9 * 9 2 6 . 1 8 6 4 5 . 2 1 8 2 . 5 * 8 7 0 . 3 * 4 5 5 . 1 1 5 6 1 . 7 6 1 3 0 . 0 5 7 7 . 0 -K P N Medain s s e n w e k s a z o tr u K 9 7 5 . 0 6 2 8 8 . 0 -8 3 7 . 0 9 1 5 . 3 1 4 4 1 . 0 4 9 9 . 0 -2 6 . 3 * 1 9 7 . 1 * 9 4 0 . 5 3 9 0 . 3 5 3 8 . 0 3 9 4 . 0 -6 1 2 . 1 * 9 0 1 . 2 * 9 5 4 . 3 7 4 4 . 7 * 9 4 1 . 2 * 9 3 3 . 4 8 1 1 . 5 * 4 7 4 . 3 * 0 1 6 . 4 1 6 8 . 5 0 1 7 5 5 . 0 -4 9 3 . 0 -E 30·tha1 CaNPK Medain s s e n w e k s a z o tr u K 4 9 3 . 0 8 4 8 8 . 0 5 9 1 . 0 8 9 . 7 1 6 0 3 . 0 -4 2 5 . 0 -6 8 8 . 6 * 7 7 2 . 2 * 2 8 2 . 4 0 4 5 . 4 * 2 6 6 . 1 * 8 7 4 . 3 0 0 6 . 3 * 3 6 9 . 2 * 9 4 2 . 9 2 0 . 5 1 * 5 4 0 . 1 4 2 0 . 1 9 0 0 . 8 * 8 3 9 . 2 * 0 5 3 . 8 0 0 0 . 6 * 5 7 4 . 3 * 7 9 6 . 2 1 K P N Medain s s e n w e k s a z o tr u K 9 0 . 3 7 3 2 9 . 0 4 0 7 . 0 8 7 . 8 1 6 1 0 . 0 6 8 9 . 0 -6 5 5 . 6 * 9 0 8 . 1 * 4 7 0 . 3 5 0 0 . 2 6 5 8 . 0 1 1 8 . 0 -6 6 . 1 3 * 4 3 0 . 2 * 2 9 1 . 4 4 7 5 . 5 2 * 1 1 8 . 1 * 0 2 7 . 4 4 6 1 . 9 * 9 0 1 . 2 * 8 4 3 . 6 0 0 9 . 5 * 3 7 7 . 4 * 9 2 8 . 3 2
110 TOMASZ SOSULSKI, EWA SZARA, MARIAN KORC, WOJCIECH STÊPIEÑ
fertilizer objects usually do not have a normal distri-bution. For this reason, the basic measure of symme-try distribution: kurtosis, skewness and median for the results obtained in different years of study at each fertilizer objects were calculated (Tab. 4). To apply for the significance of differences between objects used Kruskall-Wallis test does not require the nor-mal distribution of the data analyzed, allowing for comparison of medians for more than two objects. Since this test can not exact determine which objects fertilizer differ a significant subsequently used the Mann-Witney. This test allows comparison of medians pairs analyzed variables and assess the significance of differences. For most objects both experiments, regardless of the year of the study, there was no si-gnificance difference in the concentrations of most elements in water infiltrating the soil profile. Only the aluminum content of the water flowing out of the test object usually was significantly different (Tab. 5). Regardless of the acidification status, the amount of aluminium in the water draining from the soil fer-tilized with mineral fertilizers only (field A) was on average more than 2.5 times higher than in the water from the soil fertilized with both mineral fertilizers and manure (field E). The effect of soil acidification on the aluminium content in the groundwater was noticeable only in the field in which only mineral fer-tilization was applied (field A). The omission of soil liming (NPK combination) in that field caused an in-crease in Al content in the groundwater by about 55% in comparison with the combination that included li-ming. On the other hand, the average amounts of alu-minium in the groundwater on the limed (CaNPK)
and unlimed (NPK) plots in field E, where manure was applied every five years, were similar. This me-ans that the soil organic matter taking part in the com-plexation of aluminium determines its activity and mobility in the soil and reduces its negative effect on the crop yields obtained on unlimed plots in the expe-rimental field with combined mineral-organic fertili-zation (Mercik and Stêpieñ, 2005; Sosulski et al., 2011).
The amounts of mineral components in the gro-undwater flowing out of the plots was dependent to a lesser extent on the applied fertilization and crop ro-tation (Tab. 2). The average amounts of macro- and microelements in the water flowing out of the soil fertilized with mineral fertilizers and manure (field E) were higher than in the groundwater draining from the soil fertilized with mineral fertilizers only (field A). This is confirmed by the view, known from lite-rature, on the influence of organic fertilization on the increase in the levels of mineral components in the water infiltrating the soil profile (Baran et al., 2011; Koc, 1992).
In our study, the calcium content in the water in-filtrating the soil in the CaNPK combination in field A including in 20112012 was significantly higher than in the samples of the water flowing out of the unlimed (NPK) soil (Tab. 5). Regardless of the ferti-lization system and soil acidification status, the ave-rage calcium content in the groundwater was higher than the levels of magnesium, potassium and sodium. It should be noted that, unlike in field E, the sodium content in the groundwater in field A was similar (in the CaNPK combination) or higher (in the NPK com-r a e Y Theobjecst Ca Mg K Na Fe Zn Mn Al 1 1 0 2 AACCaaNNPPKK--AECNaPNKPK K P N E -K P N a C A K P N a C E -K P N A K P N E -K P N A K P N E -K P N a C E s n s n s n s n s n s n s n * * * * s n s n s n s n s n s n s n * * * s n * s n s n s n s n s n s n s n s n s n s n s n s n s n s n s n s n s n s n s n * * * * * s n 2 1 0 2 AACCaaNNPPKK--AECNaPNKPK K P N E -K P N a C A K P N a C E -K P N A K P N E -K P N A K P N E -K P N a C E s n s n s n s n s n s n s n s n s n s n s n s n s n s n s n s n s n s s n s n s n s n s n s n s n s n s n * s n * * s n s n * s n s n s n s n s n s n s n s n s n * s n * * * s n 2 1 0 2 -1 1 0 2 AACCaaNNPPKK--AECNaPNKPK K P N E -K P N a C A K P N a C E -K P N A K P N E -K P N A K P N E -K P N a C E * s n s n * s n s n s n s n s n s n s n s n s n s n * * * s n s n s n s n s n s n s n s n * * s n * s n s n s n s n s n * s n s n s n s n s n s n s n * s n * * * * TABLE 5. The assessment
of significance of differen-ces between the examined objects by using the Mann-Witney test
bination) than the potassium content. For almost all the plots, the average amount of zinc in the drained water was greater than the amounts of iron and man-ganese.
Worthy of note here is a very broad equivalence ratio of calcium to aluminium in the water infiltrating the profile of the test soils (Ca : Al = 12618172 :1). The value of this ratio for the arable layer of soil is taken into account when assessing plant growth con-ditions (£abêtowicz et al., 2004; Sosulski et al., 2007). However, the value of Ca:Al ratio in the solid phase of the soil in the humus accumulation horizon is nar-rower. Such a broad ratio of the two elements in gro-undwater is a manifestation of different solubilities in water of the salts of these elements, and although on the acidified plots of both experimental fields this ratio even becomes substantially narrowed down, it cannot be used in the assessment of plant growth con-ditions because of its large value.
The data in Table 6 indicate that the amount of water flowing out of the test plots in both fields was different. Considerably more water drained from field A, where lower crop yields are obtained, than from field E, where crop yields are generally higher (Mer-cik and Stêpieñ, 2005; Sosulski et al., 2011). In both years of the study, crop plants that consume different amounts of water were grown in the two experimen-tal fields: potatoes and barley in field E, and triticale and mustard in field A.
The fertilization system used in the fertilization experiments was mostly responsible for the size of the load of Ca, Mg, K, Na, Zn, Fe, Mn and Al trans-ferred from the soil to the ground water. Throughout the whole study period, leaching of magnesium, po-tassium, sodium, zinc, iron and manganese from the soil fertilized with mineral fertilizers and manure (field E) was from about 13 to 294% higher than the leaching of these components from the soil in the field where only mineral fertilizers were applied (field A). Only the load of calcium reaching the hydrosphere was similar in the two systems of fertilization. On the other hand, the amount of aluminium flowing out of field A was slightly more than twice the amount
leaving field E. The differences observed in the extent of leaching of the mineral elements lead to the conc-lusion, consistent with literature data, that organic fertilization generally increases the extent of leaching of mineral components from the soil (Baran et al., 2011; Maækowiak, 2000; Koc, 1992). In our study, this was primarily due to a higher input of nutrients to the soil in the mineral-organic than the solely mi-neral system. Despite higher crop yields in field E than in field A, and therefore greater uptake of nu-trients by plants, there is a surplus in the distribution of plant nutrients under mineral-organic fertilization. As our study shows, some of this surplus is lost from the soil through leaching. Similar amounts of calcium being washed out in both fertilization systems indi-cate, however, that the leaching of this element is as-sociated more closely with the process of soil pH adjustment than with the extent of Ca uptake by plants. In both experimental fields, lime is used in similar quantities and at similar time intervals. It is worth noting, however, that the amount of calcium flowing out of the fields with the groundwater is relatively small, especially when compared with the results obtained by other researchers (Oliveira et al., 2002; Stelle et al., 1984). At the same time, it should be noted that our study was conducted in the two expe-rimental fields in the last year before liming and in the year of liming. This certainly had an impact on the amount of the active form of that component in the soil. Indeed, it is known that the reaction of lime with acid hydrogen accumulated in the soil occurs, depending on the chemical and physical form and moisture content of the fertilizer, with varying inten-sity over a long period of time (Grzebisz, 2009). It can therefore be assumed that during the study pe-riod the pool of calcium capable of movement with water in the soil was very small.
Also of interest seem to be the results concerning the extent of aluminium leaching from the two expe-rimental fields. In the mineral fertilization system, the amount of aluminium moving from the soil to the hydrosphere was much greater than in the mineral-organic system. This is an indication of the role of -i r e p x E t n e m Fetrliziaiton (Omu3t·hlfoaw1) Ca Mg K Na Zn Fe Mn Al A manure mineral kg·ha1 g·ha1 e n o n CaNPK 1477.1 120.5 5.6 5.9 4.1 23.4 10.8 8.8 92.9 K P N 1529.0 88.2 7.7 6.3 6.4 29.3 16.2 10.6 160.9 e g a r e v a 1503.0 104.4 6.6 6.1 5.2 26.3 13.5 9.7 126.9 E 30 ·tha1 CaNPK 1456.9 119.3 7.1 15.3 6.1 30.5 28.6 17.3 60.6 K P N 1445.7 96.3 8.0 19.5 5.7 44.9 78.0 18.7 61.4 e g a r e v a 1451.3 107.8 7.6 17.4 5.9 37.7 53.3 18.0 61.0
TABLE 6. Load of mi-neral elements transfer-red from the soil into groundwater depending on fertilization and crop rotation in 20112012
112 TOMASZ SOSULSKI, EWA SZARA, MARIAN KORC, WOJCIECH STÊPIEÑ
the organic substance accumulated in the soil as a result of long-term fertilization with manure in the complexation of that element. Permanent binding of aluminium by soil organic matter does not only, as research has shown, reduce its mobility and leaching from the soil, but also, by inhibiting its activity, redu-ces the negative impact on the crop yields obtained (Mercik and Stêpieñ, 2005; Sosulski et al., 2011).
The soil acidification status had a similar effect on the relative order in terms of the size of the load of soil mineral components flowing out of the limed (CaNPK) and unlimed (NPK) plots, and their amo-unts in the groundwater. Acidification of the soil re-sulted in increased leaching of magnesium, potassium, sodium, zinc, iron, manganese (only in field A) and aluminium in comparison with the limed plots of both experimental fields. In both fertilization systems, more calcium was washed out from the limed than unlimed plots. Because the time of installation of the drainage systems made it possible to determine the extent of the outflow of soil components over 19 months in 2011 and 2012, it seemed necessary to the authors of this work to show the average monthly outflow of the analyzed soil components and in terms of per 1 m3 of the water flowing out of the soil
profi-le. The presented values allow a simulation analysis of the magnitude of the potential outflow of these elements over different periods of time and under dif-ferent soil water conditions (Tab. 7 and 8).
CONCLUSIONS
1. The amounts of mineral elements in the groun-dwater flowing out of the soil profile are sub-ject to considerable variation and are depen-dent on the volume of the outflow, the plant fertilization system and soil acidification sta-tus. In terms of the load of elements carried in the water flowing out of a Luvisol, the follo-wing relative order of concentrations can be adopted: Ca>Mg>K>Na>Al>Zn>Fe>Mn>Cu. 2. The presence of manure in the dose of fertilizers
causes an increase in the leaching of magnesium and potassium, as well as zinc, iron and mangane-se. On the other hand, organic fertilization does not increase the leaching of calcium from the soil, and reduces the activity and mobility of aluminium in the soil.
3. Depending on the plant fertilization system and soil acidification status, the following amounts are washed out with 1 m3 of water flowing out of ha a light soil: 186434 g Ca, 12.633 g Mg, 13.280 g K, 9.323.4 g Na, 29.5251 mg Al, 53184 mg Zn, 24.5319 mg Fe, and 2076.5 mg Mn.
ACKNOWLEDGEMENT
The results presented in this study were obtained through a research project NN 305 060640 funded by the Polish National Centre for Research and De-velopment in 20112014.
TABLE 8. Average load of mineral elements carried in 1 m3 of water flowing out of the field with an area of 1 ha
depending on fertilization and crop rotation -i r e p x E t n e m mFeantrulirzieaiton mineral kCga·ha1 Mg K Na gZ·nha1 Fe Mn Al A none CaNPK 6.3 294.0 308.8 217.1 1.23 0.57 0.47 4.9 K P N 4.6 404.5 331.2 334.8 1.54 0.85 0.56 8.5 e g a r e v a 5.5 349.3 320.0 276.0 1.39 0.71 0.52 6.7 E 30 ·tha1 CaNPK 6.3 374.3 804.5 321.3 1.61 1.5 0.91 3.2 K P N 5.1 422.3 1024.5 300.7 2.36 4.11 0.98 3.2 e g a r e v a 5.7 398.3 914.5 311.0 1.99 2.81 0.95 3.2 TABLE 7. Average monthly load of mineral elements transferred from the soil into groundwater depending on fertilization and crop rotation
-i r e p x E t n e m mFeantrulirzieaiton mineral gC·aha1·m3Mg K Na mZng·ha1·mF3e Mn Al A none CaNPK 271.7 12.60 13.24 9.31 52.7 24.5 19.9 209.5 K P N 185.5 16.15 13.22 13.37 61.50 34.1 22.3 338.1 e g a r e v a 228.6 14.4 13.2 11.3 57.1 29.3 21.1 273.8 E 30 ·tha1 CaNPK 434.0 25.86 55.59 22.20 110.9 103.9 63.0 220.3 K P N 394.1 32.85 79.70 23.39 183.8 319.4 76.5 251.2 e g a r e v a 414.1 29.4 48.4 22.8 147.4 211.7 69.8 235.8
REFERENCES
Baran A., Kacprzyk P., Jasiewicz C., KasperczykM., 2011. Wy-mywanie pierwiastków ladowych z gleby w zale¿noci od rodzaju nawo¿enia ³¹ki górskiej. Woda-rodowisko-Obszary Wiejskie 11(1): 1120.
Grzebisz W., 2009. Nawo¿enie rolin uprawnych. Cz. 2 Nawozy i systemy nawo¿enia. PWRiL, Warszawa: 376 pp.
Igras I., 2004. Zawartoæ sk³adników mineralnych w wodach dre-narskich z u¿ytków rolniczych w Polsce. Monografie i Roz-prawy Naukowe, IUNG, Pu³awy: 123 pp.
Koc J., 1992. Wp³yw wieloletniego nawo¿enia gnojowic¹ trzody chlewnej na zawartoæ mikroelementów w glebach i rolinach. Cz. 1 Mied, Cz. 2 Cynk. Mat. Konf. Symp. Mikroelementy w rolnictwie Wroc³aw AR: 269277.
£abêtowicz J., Rutkowska B., Szulc W., Sosulski T., 2004. Oce-na wp³ywu wapnowania oraz gipsowania Oce-na zawartoæ glinu wymiennego w glebie lekkiej. Annals UMCS Sec. E, 59 (2): 631637.
Maækowiak C., 2000. Bilans fosforu i potasu przy ró¿nym obci¹-¿eniu gnojowic¹ na podstawie wieloletnich badañ. Pamiêtnik Pu³awski Materia³y Konferencyjne 120: 302306. Mercik S., Stêpieñ W., 2005. The most important soil properties
and yields of plants in 80 years of static fertilizing experiments in Skierniewice. Fragmenta Agronomica 1(85): 189201. Misztal M., Smal H., 1991. Sk³ad chemiczny wód gruntowych
z terenów gleb uprawnych bielicowej i czarnej ziemi. Roczn. Glebozn. 3/4: 121128.
Oliveira M.W., Trivelin P.C.O., Boaretto A.E., Muraoka T., Mor-tatti J., 2002. Leaching of nitrogen, potassium, calcium and magnesium in a sandy soil cultivated with sugarcane. Pesqu-isa Agropecuaria. Brasileira 37 (16): 861868.
Pulikowski K., Kostrzewa S., Paluch J., Szewrañski S., 2007. Load of heavy metals in drainage waters in the Middle Sudety Mountains. Annals of Univ. of Life Sciences SGGW, Land Reclamation 38: 2532.
Ruszkowska M., Kusio M., Sykut S., 1999. Wymywanie pier-wiastków ladowych z gleby w zale¿noci od jej rodzaju i nawo¿enia (Badania lizymetryczne). Roczn. Glebozn. 47(1/ 2): 1122.
Sosulski T., Stêpieñ W., Mercik S., Szara E., 2011. Crop Fields and nitrogen balance in long-term fertilization experiments. Nawozy i Nawo¿enie 42: 4150.
Sosulski T., Szara E., £abêtowicz J., Przybysz M., 2007. Wp³yw wêglanu wapnia, gipsu i fosfogipsu na zawartoæ glinu w gle-bie i rolinach. Zeszyty Problemowe Postêpów Nauk Rolni-czych 533: 357368.
Steele K.W., Judd M.J., Shannon P.W., 1984. Leaching of nitrate and other nutrients from a grazed pasture. New Zealand Jour-nal of Agricultural Research 27: 511.
Westra S., Alexander L.V., Zwiers F.W., 2013. Global increasing trends in annual maximum daily precipitation. Journal of Cli-mate 26: 39043918.
Received: July 1, 2013 Accepted: November 21, 2013
Wymycie makroelementów, mikroelementów i glinu z gleby w warunkach wieloletnich
dowiadczeñ nawozowych w Skierniewicach (rodkowa Polska)
Streszczenie: Celem pracy by³a ocena zawartoci sk³adników mineralnych w wodzie gruntowej i wielkoæ ich odp³ywu z pola w ró¿nych systemach nawo¿enia: mineralnego i mineralno-organicznego. W 2011 r. na wybranych obiektach wieloletnich dowiadczeñ nawozowych zlokalizowanych na Polu Dowiadczalnym Wydzia³u Rolnictwa i Biologii SGGW w Skierniewicach zainstalowano systemy drenarskie zbieraj¹ce wodê gruntow¹ z poletka. Systemy takie zainstalowano na obiektach wapnowanych (CaNPK) i nie-wapnowanych (NPK) dwóch eksperymentów, na których stosowane jest nawo¿enie w systemie nawo¿enia mineralnego (ekspery-ment A) i mineralno-organicznego (ekspery(ekspery-ment E). W ramach badañ zmierzono wielkoæ odcieku wody oraz zawartoæ Ca, Mg, K, Na, Zn, Fe, Mn, Cu i Al w próbach wody. Zawartoæ sk³adników mineralnych w wodzie odp³ywaj¹cej z profilu gleby ulega znacznym wahaniom i jest uzale¿nione od wielkoci odp³ywu, systemu nawo¿enia rolin i stanu zakwaszenia gleby. W zale¿noci od zawartoci pierwiastków w wodzie odp³ywaj¹cej z gleby p³owej mo¿na przyj¹æ wiele stê¿eñ pierwiastków: Ca>Mg> K>Na>Al>Zn>Fe>Mn>Cu. Udzia³ obornika w dawce nawozów powoduje wzrost wymycia magnezu i potasu oraz cynku, ¿elaza i manganu. Natomiast nawo¿e-nie organiczne nawo¿e-nie wp³ywa na zwiêkszenawo¿e-nie wymycia wapnia z gleby i ogranicza aktywnoæ i mobilnoæ glinu w glebie. W zale¿-noci od sposobu nawo¿enia rolin oraz stanu zakwaszenia gleby wraz z 1 m3 wody odp³ywaj¹cej z gleby p³owej zostaje wymyte z ha: 186434 g Ca, 12,633 g Mg, 13,280 g K, 9,323,4 g Na, 29,5251 mg Al, 53184 mg Zn, 24,5-319 mg Fe i 2076,5 mg Mn.
