Mobility of Cd, Pb, Cu, and Cr in some Estonian soil types/ Cd, Pb, Cu ja Cr mobiilsus monedes Eesti muldades.
Contamination of soil with heavy metals is a common environmental problem related to industrial activity and agricultural practices, i.e. wastewater irrigation and composts, application of fertilizers and agro-chemicals, disposal of sewage sludge (Punning & Varras 1993; Sterckeman et al. 2000; Han et al. 2001; Twardowska 2004; Weber et al. 2007). Heavy metals discharged to soil are generally characterized by long residence times (Alloway 1995; Selim & Amacher 1997). Metals can be accumulated in the upper layer of the soil or penetrate in different forms into surface water (Keller & Domergue 1996; Citeau et al. 2003; Lepane et al. 2007). Sorption and precipitation are fundamental chemical reactions of trace elements that greatly affect metal availability in aerobic terrestrial systems (Brad12004). The infiltration of surface water is one possible way of contamination of soil and groundwater by mobile metals (Singh & Steinnes 1994; Qiang et al. 2006). Metals in dissolved forms are more bioavailable and consequently constitute the greatest environmental hazard (Kalbitz & Wennrich 1998; Kookana & Naidu 1998; Turner et al. 2008). Metals can be transported along the soil profile by colloids or in dissolved forms depending on the metal concerned (Citeau et al. 2003; Zhao et al. 2009). In general, metal mobilization depends on the concentration of the parent metal in the soil solution, which in turn depends on the sorption and retention of the same metal in soil (Singh & Steinnes 1994; Alloway 1995; Sterckeman et al. 2000).
It is well known that basic soil characteristics influencing the sorption of metals are pH, redox potential, contents of organic matter, clay, Fe and Mn oxides and hydroxides, and metal carbonates (Selim & Amacher 1997; Bradl 2004; Vega et al. 2006; Usman 2008). Recent studies have established significant impact of mineral components such as carbonates on the sorption and retention of metals (Shirvani et al. 2006; Ahmed et al. 2008; Sipos et al. 2008). However, the role of carbonates in affecting the fate of toxic metals in soils is not yet fully clear.
As a rule, soil properties and composition change with depth. Consequently, the characteristics of subsoil could be different from those of the surface layer. The subsoil layer has been shown to be an important geochemical barrier against the migration of metals in the soil system, including penetration into groundwater (Elliott et al. 1986; Hooda & Alloway 1998; Sterckeman et al. 2000).
An abundant literature is available on the sorption of heavy metals by surface soils, but data concerning the whole soil system are lacking. The estimation of the risk derived from heavy metals contamination in soils requires better knowledge about metal interaction in soil.
The aim of the present work is to evaluate the capacity of subsoil for selected heavy metals (Cd, Pb, Cu, Cr) using experimentally derived distribution coefficients ([K.sub.d]). Five soils, representing four important soil types in Estonia, Rendzic Leptosol (Rendzinas), Podzol (Sod-podzolic), Podzoluvisol (Brown pseudopodzolic), and Podzolic Gleysols (Gley-podzols), were investigated (Table 1). The paper is an extension of our previous study (Alumaa et al. 2001) on topsoil (A horizon) samples from the parent soil types.
MATERIALS AND METHODS
Samples of soils were taken from the C horizon in different locations in Estonia (Table 1). A detailed sampling procedure is described in Petersell et al. (1996).
The subsoil samples were wrapped in plastic bags and transported to the laboratory. All samples were airdried, crushed, and sieved through a 2 mm mesh. The fraction less than 2 mm was taken for the sorption experiments.
Soil pH was measured using a 1:2 suspension of soil/water. The content of soil organic matter (OM) was found by the mass difference (weight loss) upon heating air-dry soil (105[degrees]C for 3 h) to 340[degrees]C in a muffle furnace for 2 h.
Batch equilibrium experiments were used in order to compare metal affinity differences between the subsoil matrices. The experiments were carried out using 50 mL test tubes. Two grams of the air-dried sample was added to each test tube along with 10 mL of parent metal solution in 0.01 M Ca[Cl.sub.2]. The ranges of initial concentrations of Cd, Pb, Cu, and Cr are presented in Table 2.
After 16 h of shaking at room temperature (21[degrees]C), the samples were separated by centrifugation at 3000 rpm for 10 min and the supernatant was analysed by graphite furnace AAS. The metal solutions were prepared from the stock solution of metal salts (chlorides) by adding the required amount of the stock solution to 0.01 M Ca[Cl.sub.2].
The native amount of the metal involved in the sorption process was characterized by extracting the soil sample with 0.01 M Ca[Cl.sub.2]. The amount of the metal adsorbed was calculated from the difference between concentrations in the initial and the equilibrium solution. Blank tests without a sample but applying the same procedure for the sorption were carried out in parallel for each set of analysis.
RESULTS AND DISCUSSION
Soil properties (C horizon)
The main properties of subsoil samples are presented in Table 3. The pH values were almost neutral. The mineral composition of samples was characterized by high variation of quartz, clay, calcite, dolomite, and Fe/Mn content.
Isotherms of metal sorption by subsoil were calculated by plotting equilibrium concentrations of the metal against adsorbed amounts. The data fitted well to the linear Freundlich isotherm. The distribution coefficient ([K.sub.d]) was then found using the relation [K.sub.d] = [C.sub.s]/[C.sub.w], where [C.sub.s] is the concentration of the metal adsorbed in the soil at equilibrium and [C.sub.w] is the concentration of the metal in the solution at equilibrium. The [K.sub.d] values for each metal are presented in Table 4. The sequence of sorption affinity of metals toward subsoils was found to be the following: Pb > Cr > Cu > Cd for Podzoluvisol, Cr > Pb > Cu >> Cd for Podzol, Pb > Cu >> Cr > Cd for Podzolic Gleysols, Pb >> Cu, Cd >> Cr for Rendzic Leptosol.
As expected, the results obtained revealed an important role of the soil type, i.e. pH and composition in immobilization of Cd, Pb, and Cu in subsoil samples. Cd and Pb demonstrated high affinity towards subsoils, which had the highest content of carbonates and Mn-containing components (Table 3). Hooda & Alloway (1998) observed similar trends when investigating the sorption of Cd and Pb in different soils in England.
A positive significant correlation was detected between Cr adsorption and content of quartz (R = 0.90, p < 0.05), whereas for Cd the relationship was negative (R = -0.92, p < 0.05). It means that Cr had the highest affinity to subsoil (sample 2) with the highest content of OM and quartz.
The results of the present study on heavy metal sorption in subsoils were compared with early data obtained for parent topsoil samples. The main characteristics of topsoil samples are presented in Table 5. The data demonstrated higher affinity of Cd, Pb, and Cu towards topsoil samples (Table 6), with a high content of carbonates and Fe/Mn components. Cr sorption was affected by the significant amount of OM and quartz in topsoil samples. A significant (p < 0.05) positive correlation was estimated between Cd (R = 0.94), Pb (R = 0.93), Cu (R = 0.93) and the content of Mn, which indicated the prevalent role of Mn oxides in the accumulation of these metals.
On the basis of the adsorption characteristics it is possible to evaluate in-depth penetration of each metal (Carlon et al. 2004; Sastre et al. 2007). In general, soils with a high sorption affinity and retention for a trace metal have a significant capacity for surface accumulation of the metal concerned. The metal pollution of topsoil may have long-lasting effect on the mineralization of OM and nutrient cycling in the soil ecosystem via change in the microbiological properties of soil (Kandeler et al. 2000).
Metal leaching through the boundary between topsoil and subsoil increases soil-bound and/or dissolved metal in subsoil (Citeau et al. 2003). If subsoil has a high affinity for a metal, the retention of the metal leached from the surface soil is efficient and its further penetration to groundwater could be prevented. On the contrary, if the adsorption is low, subsoil is an inefficient barrier against groundwater contamination. Finally, if the adsorption capacity of both topsoil and subsoil is low, soil as a whole offers low protection against groundwater contamination by metals deposited to the soil surface from air pollution, fertilizer application, or other sources.
The great difference between the Cd and Cu sorption ability of topsoil and subsoil of Podzoluvisol (sample 1) (Tables 4 and 6) could be an indicator of the following processes: the metals leached from the surface soil layer could be accumulated in subsoil. This soil has high affinity for both Pb and Cr and consequent possible accumulation of metals in soil.
The low Cd sorption capacity of Podzol (sample 2) indicates that the metal present in the surface layer could be readily leached to groundwater. The observed behaviour of Cd is in good agreement with the study of Keller & Domergue (1996), who also found that the metal could be transported in depth through a Podzolic soil. On the other hand, the much higher adsorption capacity of subsoil for Pb, Cr, and Cu (Table 4) compared to topsoil (Table 6) show that these metals could be readily accumulated in subsoil.
Podzolic Gleysols (sample 3) exhibit a certain affinity in subsoil for Cu and only moderate affinity for Pb and Cd (Tables 4 and 6). This soil has only moderate retention capacity for Pb and Cu in the surface layer, but much higher values in the subsoil, where accumulation of these metals would be expected. The low affinity of soil towards Cr indicates the risk of contamination of groundwater with this metal.
It is interesting to compare the different behaviour of metals in two Rendzic Leptosol samples. Cu in sample 4 would be retained mainly in the surface layer, whereas in sample 5 this metal could penetrate into deeper layers and accumulate there. Sample 5 has a sufficiently high Cd adsorption capacity of the surface layer to predict accumulation there. In sample 4 the leaching of the metal from the surface layer and its subsequent retention in subsoil with a high content of calcite is a more likely outcome. The adsorption capacity for Cr is low in both samples and water could be easily contaminated by this metal. As a consequence, plants growing in contaminated soils could represent a significant pathway for human exposure to toxic metal (Kabata-Pendias 2004; Khan et al. 2008).
The two Rendzic Leptosol soils (samples 4 and 5) exhibit a higher sorption affinity for Pb and Cd than the other soils. The very high sorption capacity of Pb in these soils would indicate an extremely high possibility of metal accumulation and retention, which affect metal mobility and toxicity. Several studies on the sorption of heavy metals added to soils and minerals have inferred a higher Pb affinity relative to other metals (Elliott et al. 1986; Anderson & Christensen 1988; Veeresh et al. 2003; Vega et al. 2006; Sastre et al. 2007; Zhang & Zheng 2007; Usman 2008). This phenomenon is explained by specific properties of the metal concerned, i.e., higher ionic radius, atomic weight, greater hydrolysis constant, etc., and the formation of hydrolysis products of (MeO[H.sup.+]). The removal of OH- ions from the solution by the precipitation of the metal as Me[(OH).sub.2] is also an important issue (Usman 2008).
The adsorption of selected heavy metals (Cd, Pb, Cu, and Cr) in four soil types was studied. An important role of calcites and dolomites in the immobilization of metals in soils was revealed. Due to different sorption affinity of topsoil and subsoil for toxic metals in Podzol, an increase in dissolved Cd in the surface layer and accumulation of other metals in subsoil could be expected. The accumulation of toxic lead could occur in soils with a high content of dolomite. The results indicate the potential risk of groundwater contamination with toxic metals in every studied soil type.
Acknowledgements. This study was supported by the Research Council of Norway (Project No. 120400/730), Estonian Research Council Targeted Financing Project SF0690001s09, and Estonian Science Foundation (grant No. 6828). The authors express their thanks to Dr Torill Eidhammer Sjobakk for help with the experimental part of the work and to P. Laas for technical assistance. The critics, comments, and valuable recommendations of the two reviewers are greatly appreciated.
Received 11 February 2009, accepted 6 April 2009
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Natalya Irha (a), Eiliv Steinnes (b), Uuve Kirso (a), and Valter Petersell (c)
(a) National Institute of Chemical Physics and Biophysics, Akadeemia tee 23, 12618 Tallinn, Estonia; firstname.lastname@example.org
(b) Norwegian University of Science and Technology, Department of Chemistry, N-7491 Trondheim, Norway
(c) Geological Survey of Estonia, Kadaka tee 80/82, 12618 Tallinn, Estonia
Table 1. Characterization of the studied soil types. Classification of parent matter according to Petersell et al. (1997). Samples of soil 5 were collected from the B-C horizon because monolithic Silurian dolomite occurs deeper than 60 cm Sample Soil type Site Parent matter Depth, cm No. 1 Podzoluvisol Tooma-15 Sand and silt 100-120 2 Podzol Tartu-41 Sandy till 100-120 3 Podzolic Gleysols Kasari-26 Till and silt 110-130 4 Rendzic Leptosol Papiaru-1 Till 90-110 5 Rendzic Leptosol Arase-1 Local till 50-60 Table 2. The ranges of initial concentrations of metals ([micro]g [mL.sup.-1]; for Cd, ng [mL.sup.-1]) in sorption experiments Metal The range of initial concentrations Cd 7-74 Pb 6-129 Cu 1-61 Cr 0.2-15.6 Table 3. The characteristics of subsoil samples (data on the mineral composition and Fe/Mn content after Petersell et al. 1996). For the numbering of soil types see Table 1 Composition, Soil sample % 1 2 3 4 5 Clay 7 16 4 12 15 Quartz 35 69 31 16 22 Calcite 37 2 31 56 7 Dolomite 9 1 17 3 44 OM 0.2 1.2 0.2 0.7 0.1 Mn * 176 440 278 425 464 Fe 0.62 2.21 0.99 1.03 1.58 pH (H2O) 7.1 6.9 7.2 7.2 7.1 * Mn in ppm; OM, organic matter. Table 4. Adsorption of metals in subsoil samples according to [K.sub.d] values (mL [g.sup.-1]) with standard deviations. For the numbering of soil types see Table 1 Soil sample Cd Pb 1 1 040 [+ or -] 63 9 660 [+ or -] 434 2 33 [+ or -] 2 4 090 [+ or -] 230 3 1 060 [+ or -] 457 21 500 [+ or -] 142 4 2 390 [+ or -] 104 > 61 600 5 1 350 [+ or -] 170 61 600 [+ or -] 471 Soil sample Cu Cr 1 2 360 [+ or -] 340 6 010 [+ or -] 92 2 1 220 [+ or -] 144 7 780 [+ or -] 558 3 10 090 [+ or -] 1 253 820 [+ or -] 178 4 3 670 [+ or -] 529 269 [+ or -] 53 5 1 640 [+ or -] 94 870 [+ or -] 55 Table 5. The characteristics of topsoil samples (after Petersell et al. 1996). For the numbering of soil types see Table 1 Composition, Soil sample % 1 2 3 4 5 Clay 8 15 21 13 12 Quartz 60 34 32 29 26 Calcite 5 nd 9 15 2 Dolomite 2 nd 6 nd 14 OM 6.64 4.88 18.64 6.86 6.93 Mn * 330 280 470 688 880 Fe 0.93 1.24 2.34 2.28 2.26 pH ([H.sub.2]O) 7.4 6.5 5.0 7.1 7.12 * Mn in ppm; nd, not determined; OM, organic matter. Table 6. Adsorption of metals in topsoil (A horizon) samples based on values of the distribution coefficient, [K.sub.d] (n [+ or -] SD), mL [g.sup.-1], for parent metal. In parentheses: n - [K.sub.d] value, SD--standard deviation. For the numbering of soil types see Table 1. (Data adopted from Alumaa et al. 2001) Soil sample Cd Pb 1 486 [+ or -] 34 6 250 [+ or -] 125 2 88 [+ or -] 6 308 [+ or -] 6 3 1 260 [+ or -] 8 5 420 [+ or -] 108 4 1 250 [+ or -] 236 > 61 6004 5 2 650 [+ or -] 186 > 61 600 Soil sample Cu Cr 1 473 [+ or -] 52 1 020 [+ or -] 92 2 58 [+ or -] 6 537 [+ or -] 48 3 235 [+ or -] 26 1 100 [+ or -] 99 4 150 [+ or -] 1 743 577 [+ or -] 190 5 11 200 [+ or -] 1 561 295 [+ or -] 86
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|Author:||Irha, Natalya; Steinnes, Eiliv; Kirso, Uuve; Petersell, Valter|
|Publication:||Estonian Journal of Earth Sciences|
|Date:||Sep 1, 2009|
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