Abstract:A model is described that may help to resolve uncertainty and controversy over the long-term consequences of sludge applications to arable land, especially with regard to the effects of sludge adsorption characteristics on trace metal solubility and bioavailability (e.g., the sludge "time bomb" or sludge "protection" hypotheses). Mass balances of organic and inorganic material derived from sludge and crop residues are simulated. Each pool has a potentially different adsorption affinity for trace metals, and th… Show more
“…Increasing Cd input generally resulted in increasing Cd plant at three out of four sites. However, similar to Cd DGT , plant Cd uptake has been shown to vary widely with slight changes in soil physical and chemical parameters (Bergkvist and Jarvis, 2004 and Wang et al, 2006). …”
Cadmium is a common impurity in phosphatic fertilizers and may contribute to soil Cd accumulation. Changes in total and bioavailable Cd burdens to agricultural soils and the potential for plant Cd accumulation resulting from fertilizer input was investigated. Three year field studies were conducted using three dose levels of cadmium-rich, commercial, phosphate fertilizers applied at four agricultural sites. Labile Cd concentrations, measured using the passive sampling device Diffusive Gradients in Thin Films (CdDGT), increased with increasing fertilizer application rates. Cd also accumulated in the edible portion of wheat and potato crops grown at the sites, and showed strong positive dose response with fertilizer treatment. Regression models were calculated for each site, year, and for individual crops. Model comparisons indicated that soil physical and chemical parameters in addition to soil Cd fractions, were important determinants of CdDGT. Significant factors contributing to CdDGT concentrations were Cd from fertilizer input (Cdfertilizer), pH, cation exchange capacity (CEC), and total recoverable Cd (Cdtotal). Important factors used to determine Cd concentrations in wheat grain (Cdwheat) and in potato (Cdpotato) were as follows: Cdwheat:Cdfertilizer, and CdDGT; and Cdpotato:Cdfertilizer, CdDGT, % O.M. The effective concentration, CE, calculated from DGT did not correlate well with Cdwheat or with Cdpotato. Direct measurements of CdDGT correlated better with Cd found in edible plant tissue. The modeling approach presented in this study helps to estimate Cd accumulation in plant tissue over multiple years and in distinct agricultural soil systems.
“…Increasing Cd input generally resulted in increasing Cd plant at three out of four sites. However, similar to Cd DGT , plant Cd uptake has been shown to vary widely with slight changes in soil physical and chemical parameters (Bergkvist and Jarvis, 2004 and Wang et al, 2006). …”
Cadmium is a common impurity in phosphatic fertilizers and may contribute to soil Cd accumulation. Changes in total and bioavailable Cd burdens to agricultural soils and the potential for plant Cd accumulation resulting from fertilizer input was investigated. Three year field studies were conducted using three dose levels of cadmium-rich, commercial, phosphate fertilizers applied at four agricultural sites. Labile Cd concentrations, measured using the passive sampling device Diffusive Gradients in Thin Films (CdDGT), increased with increasing fertilizer application rates. Cd also accumulated in the edible portion of wheat and potato crops grown at the sites, and showed strong positive dose response with fertilizer treatment. Regression models were calculated for each site, year, and for individual crops. Model comparisons indicated that soil physical and chemical parameters in addition to soil Cd fractions, were important determinants of CdDGT. Significant factors contributing to CdDGT concentrations were Cd from fertilizer input (Cdfertilizer), pH, cation exchange capacity (CEC), and total recoverable Cd (Cdtotal). Important factors used to determine Cd concentrations in wheat grain (Cdwheat) and in potato (Cdpotato) were as follows: Cdwheat:Cdfertilizer, and CdDGT; and Cdpotato:Cdfertilizer, CdDGT, % O.M. The effective concentration, CE, calculated from DGT did not correlate well with Cdwheat or with Cdpotato. Direct measurements of CdDGT correlated better with Cd found in edible plant tissue. The modeling approach presented in this study helps to estimate Cd accumulation in plant tissue over multiple years and in distinct agricultural soil systems.
“…Not reaching the maximum copper concentration for both sewage sludges is an indication that sewage sludges adsorb a large quantity of copper and potentially other heavy metals. Bergkvist and Jarvis (2004) found that soils amended with sewage sludge have a very high adsorption capacity with regard to cadmium. Liu and Wang (2004) studied in situ speciation of copper-humic substances in a contaminated soil during electrokinetic remediation and found that copper-humic substances were associated with 50% of the total copper contained in the soil.…”
Section: Vol 171~no 1 Copper Mobility In Soil and Sewage Sludges 35mentioning
“…It is not clear to what extent preferential flow will contribute to metal leaching at the field scale. Bergkvist & Jarvis (2004) attributed the difference between modelled and observed Cd profiles in a well-structured clay loam soil, amended with sewage sludge, to the effects of macropore transport.…”
Leaching of Cd and Zn in polluted acid, well-drained soils is a critical pathway for groundwater pollution. Models predicting future groundwater contamination with these metals have rarely been validated at the field scale. Spodosol profiles (pH 3.2-4.5) were sampled in an unpolluted (reference) field and in a field contaminated with Cd and Zn through atmospheric deposition near a zinc smelter. Average metal concentrations in the upper horizons were 0.2 mg Cd kg À1 and 9 mg Zn kg À1 in the unpolluted field, and 0.8 mg Cd kg À1 and 71 mg Zn kg À1 in the contaminated field. Isotopic dilution was used to measure the labile concentration of Cd and Zn, and the metal transport was modelled using measured sorption parameters that describe the distribution between the labile metal pool (instead of the total metal pool) and the solution phase obtained by centrifugation. Solutions were also collected by wick samplers in two polluted and one unpolluted profile at a depth of 70 cm. Concentrations in these solutions were in the order of 15 mg Cd litre À1 and 0.8 mg Zn litre À1 for the polluted profiles, and 1 mg Cd litre À1 and 0.04 mg Zn litre À1 for the unpolluted profile. The concentrations in these solutions agreed well with those in soil solutions obtained by centrifugation, which supported the use of the local equilibrium assumption (LEA). Present-day Cd profiles in the polluted field were calculated with the LEA, based on the emission history of the nearby smelter and taking spatial variability into account. Observed and predicted depth profiles agreed reasonably well, but total Cd concentrations in the topsoil were generally underestimated by the model. This may be attributed to the presence of non-labile Cd in the atmospheric deposition, which was not accounted for in the retrospective modelling. The large concentrations of nonlabile Zn in the topsoil of the polluted field were also indicative that metals in the atmospheric deposition were (partly) in a sparingly soluble form, and that release of these non-labile metals is a slow process. The presence of non-labile metals should be taken into account when evaluating metal mobility or predicting their transport.
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