Bioturbation-Driven Release of Buried PCBs and PBDEs from Different Depths in Contaminated Sediments

Josefsson, Sarah; Leonardsson, Kjell; Gunnarsson, Jonas S.; Wiberg, Karin

doi:10.1021/es100615g

Cited by 77 publications

(47 citation statements)

References 52 publications

(80 reference statements)

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“…Thus sediments have become a major reservoir of HOCs. 2,3 When exogenous inputs diminish, sequestered HOCs can be released from sediments via resuspension, molecular diffusion, 4 bioturbation, 5 gas ebullition, 6 tidal rush, etc., resulting in net fluxes from sediments to overlying water. Among these transport pathways, only molecular diffusion mainly involves the freely dissolved chemicals and is a direct reflection of the chemical fugacity difference between the two phases.…”

Section: ■ Introductionmentioning

confidence: 99%

Novel Passive Sampling Device for Measuring Sediment–Water Diffusion Fluxes of Hydrophobic Organic Chemicals

Liu

Bao

Zhang

et al. 2013

Environ. Sci. Technol.

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Molecular diffusion across the sediment−water interface, as one of the key geochemical processes, dictates whether a sediment is a source or sink of chemicals, providing useful data in designing remedial actions. Despite ample previous efforts in quantifying sediment−water diffusion fluxes, the resulting methods are largely unsatisfactory. Herein, we introduce a novel passive sampling device capable of measuring vertical profiles of chemical concentrations near the sediment−water interface, from which diffusion fluxes can be calculated based on a model that we developed. In laboratory testing, diffusion fluxes (0.032−310 ng m −2 d −1 ) of dichlorodiphenyltrichloroethane and its metabolites obtained from the present sampling device were consistent with those (0.38− 610 ng m −2 d −1 ) determined by using a conventional active sampling method, solid-phase extraction/liquid−liquid extraction. Field deployment of the sampling device yielded individual diffusion fluxes of p,p′-DDD, p,p′-DDE, p,p′-DDMU, o,p′-DDMU, p,p′-DDNU, and p,p′-DBP in the range of 5.9−150 ng m −2 d −1 , which were comparable to those (5.5−85 ng m −2 d −1 ) obtained with a benthic chamber. Moreover, diffusion fluxes of p,p′-DDT and o,p′-DDT obtained with the sampling device were negative; i.e., the sediment is acting as a sink for these chemicals, while that could not be found using the benthic chamber. Thus, the passive sampling device can provide better information about the movement of chemicals through the sediment and overlying water for the choice of remedial strategies.

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Section: ■ Introductionmentioning

confidence: 99%

Novel Passive Sampling Device for Measuring Sediment–Water Diffusion Fluxes of Hydrophobic Organic Chemicals

Liu

Bao

Zhang

et al. 2013

Environ. Sci. Technol.

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“…Furthermore, substantial amounts of sludge applied to land are bound to enter aquatic environments, due to soil erosion. Although it can be expected that sludge particles will rapidly settle on the water basin floor, the ability of benthic animals to re-mobilize brominated flame retardants from sediments, can create a secondary pollution source [37]. Thereafter, the re-mobilized BDE 209 can be de-brominated by aquatic biota [35,36].…”

Section: Discussionmentioning

confidence: 99%

Distribution of Polybrominated Diphenyl Ethers in Sewage Sludge, Sediments, and Fish from Latvia

2017

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Abstract:The polybrominated diphenyl ethers (PBDEs) are bioaccumulative, persistent, and toxic. They have a high risk of emission into the environment via volatile losses and diffuse sources, such as commercial product disposal or the use of sewage sludge. The PBDEs' congeners were analyzed in municipal waste water treatment plant (WWTP) sludge, river and lake water, sediment, and fish samples, to investigate the concentrations in urban and natural locations. The sum of eight PBDE congener (∑ 8 PBDE 28,47, 99, 100, 153, 154, 183, 209) concentrations in WWTP sludge varied from 78 ng·g −1 DW, to 714 ng·g −1 DW. The BDE 209 constituted up to 93%-98% of ∑ 8 PBDE. In water, the concentrations of all of the measured PBDE congeners were below the limit of detection. Similarly, the concentration of BDE 209 in the sediments was below the limit of detection in all samples. The sum of seven PBDE congener concentrations in the sediments varied from 0.01 to 0.13 ng·g −1 DW. The sum of eight PBDE congener concentrations in fish (European perch) tissues varied from 0.13 to 0.82 ng·g −1 WW. As was recorded for the WWTP sludge, the BDE 209 was the dominant congener, constituting 24%-93% of ∑ 8 PBDE. The sum of seven PBDE congener concentrations, excluding BDE 209, as well as the concentrations of BDE 209 that were measured in WWTP sludge, exhibited a weak negative correlation (Pearson's r = −0.56, p = 0.1509 and r = −0.48, p = 0.2256, respectively) with the content of dry matter in the sludge. The sum of seven PBDE congener concentrations measured in sediments exhibited a strong negative correlation (Pearson's r = −0.82, p = 0.0006) with the content of dry matter in the sediments, and a strong positive correlation (Pearson's r = 0.68, p = 0.0109) with the total carbon content. The obtained results indicated that the fine-grained WWTP sludge particles, with a larger relative surface area, adsorbed BDE 209 the most effectively. This finding was supported by the relatively low environmental concentrations of PBDE congeners, especially BDE 209, which can be explained by the lack of using sewage sludge in agricultural application in Latvia. Furthermore, it seems that, at present, the observed differences in the PBDE congener concentrations in sediments can be attributed to differences in the physical-chemical properties of sediments.

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“…In systems with bioturbators, free heavy metal concentration in pore water just below the sediment-water interface were much lower than the treatment without bioturbators, probably because the formation process of iron and manganese hydrous oxides enhanced by bioturbation, tends to sorb or coprecipitated heavy metals (Ciutat and Boudou 2003). Therefore, bioturbation in sediment are important factors influencing chemical-diffusion fluxes across the sediment-water interface (Josefsson et al 2010;Thibodeaux 2005). However, the presence of Chironomid larvae generally increased the free heavy metals concentrations in pore water, especially in the deeper layers, indicating that organisms in sediment increase the chemicaldiffusion flux through bioturbation.…”

Section: Effects Of Ac Amendments and Bioturbation On Heavy Metals Flmentioning

confidence: 99%

“…However, most earlier studies addressed the effectiveness of AC on remediation of HOCs contaminated sediment (Cho et al 2009;Kupryianchyk et al 2013), whereas the effectiveness on heavy metals has been studied less frequently. Bioturbation can influence the fate, transport, and bioavailability of sediment-bound heavy metals (Ciutat and Boudou 2003;Schaller 2014), it may be responsible for a major fraction of the pollutants released from sediments to the water column (Cardoso et al 2008;Josefsson et al 2010;Thibodeaux and Bierman 2003). In addition, bioturbation may affect sediment remediation processes because it is a main process controlling mobilization of elements including dissolved organic carbon (DOC) from sediments (Schaller 2014).…”

Section: Introductionmentioning

confidence: 99%

Bioturbation effects on heavy metals fluxes from sediment treated with activated carbon

Men

Yang

et al. 2016

Environ Sci Pollut Res

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Adding activated carbon (AC) to sediment has been proposed as an in situ sediment remediation technique. To date, it is not clear whether this technique is effective in the treatment of heavy metal-contaminated sediment in the presence of bioturbators. In the present study, we compare the ability of granular-activated carbon (GAC) and powderactivated carbon (PAC) to reduce Cu, Zn, and Pb pore water concentrations at environmentally relevant concentrations in the absence and presence of Chironomid larvae. Compared to untreated sediment, PAC and GAC addition in the absence of Chironomid larvae resulted in reductions of free Cu concentrations of 78 and 66 % just below the sediment-water interface after 28 days, respectively. While for Pb and Zn these concentration reductions were only 40 and 38, 19 and 25 %, respectively. The presence of Chironomid larvae in untreated, and GAC sediment generally increased the free heavy metals concentrations in pore water, especially in the deeper layers. In comparison with untreated sediment, the coexistence of AC enhanced the accumulation of heavy metals, especially for PAC. This increased bioaccumulation may decrease the survival of Chironomid larvae. The result indicated that ACs may not be suitable for the remediation of heavy metalcontaminated sediments.

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Bioturbation-Driven Release of Buried PCBs and PBDEs from Different Depths in Contaminated Sediments

Cited by 77 publications

References 52 publications

Novel Passive Sampling Device for Measuring Sediment–Water Diffusion Fluxes of Hydrophobic Organic Chemicals

Novel Passive Sampling Device for Measuring Sediment–Water Diffusion Fluxes of Hydrophobic Organic Chemicals

Distribution of Polybrominated Diphenyl Ethers in Sewage Sludge, Sediments, and Fish from Latvia

Bioturbation effects on heavy metals fluxes from sediment treated with activated carbon

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