EDDS enhanced Shewanella putrefaciens CN32 and α-FeOOH reductive dechlorination of carbon tetrachloride
Graphical abstract
Introduction
It has reported that microbial reduction of iron oxides by dissimilatory iron-reducing bacteria (DIRB) has been acknowledged as a significant process in anaerobic environments (Li et al., 2010, Bae and Lee, 2012). It was generally believed that there were two mechanisms for electron transfer between bacterial cells and Fe (III) surfaces: through ligands which solubilize Fe(III) by complex formation; by redox cycling of electron shuttle between the bacterial cell and Fe(III) surface (Esther et al., 2014). The bio-reduction rate and extent of Fe(III) oxide was influenced by many factors, for example, the composition of the culture medium; availability; surface area and crystallinity; microbial community structure and biomass; and the adsorption affinity with iron oxides and bacteria (Glasauer et al., 2001).
Available literature provided evidence that the rate of bio-reduction was higher for amorphous Fe(III) than crystalline Fe(III) (Eric E. Roden and Zachara†, 1996). The decrease in bio-reduction rate of Fe(III) oxide could be attributed to the adsorption or precipitation of accumulation Fe(II) which blocking reaction dissolution sites of Fe(III) oxides (Royer et al., 2004). Delaying in sorption or precipitation of surface-bound Fe(II) could further accelerate the bio-reduction of Fe(III) oxide to form surface-bound iron species (Royer et al., 2002). Attempts were made to add ligands such as citric acid complexes agent, EDTA and NTA, followed by its solubilization on the oxide surface or the biological Fe(II), keeping Fe2+ in soluble form and thereby preventing Fe2+ adsorption (Taillefert et al., 2007, Manzella et al., 2013). In addition, the formation of Fe-ligand complexes affected the redox potential of the Fe2+/Fe3+ which was direct relevance to the remediation of contaminated environmental systems (Song et al., 2017).
Despite the fact that previous study reported the dissolution of Fe(II) can be combined with the polycarboxylic acid on the surface of the iron oxide to form surface bound Fe(II) (adsorbed Fe(II)–polycarboxylic ligand complexation) (Roden, 2004), however the mechanism of formation surface bound Fe(II) (Fe(II)–ligand complexation) on the surface of the iron oxide was still unknown. It was also known that carboxylic acid such as ethylenediamine tetra acetic acid (EDTA) could prevent iron precipitation even at neutral pH. However, the widespread use of EDTA might lead to some undesirable environmental consequences because of its poor biodegradability and strong heavy metal chelating capacity (Englehardt et al., 2007, Prieto et al., 2013). Recently, (S,S)-N,N0-ethylenediamine disuccinic acid (EDDS), as a structural isomer of EDTA, has been successfully applied to the remediation of heavy metal contaminated soils instead of traditional chelating agents such as EDTA or NTA (Attinti et al., 2017, Beiyuan et al., 2017). One of the main advantages of EDDS that has enhanced its use for soil washing of potentially toxic metals in contaminated soils is certainly its biodegradability (Meers et al., 2005, Leštan et al., 2008). Iron-reducing reaction has recently been recognized as an important process under anaerobic conditions, especially in Fe-bearing soil. So the widely application of EDDS may affect the iron reduction process in contaminated sites. Although previous study considered the interactions between EDDS and soil minerals (Yip et al., 2009), However, to date, there are few studies reported that EDDS improve bio-reduction efficiency of iron oxides by DIRB and stimulate the generation of surface-bound Fe(II). Several studies have reported the importance of surface-bound iron species to the abiotically reductive transformation of chlorinated hydrocarbons (Tobler et al., 2007, Maithreepala and Doong, 2009). So the addition of EDDS may also effect the removal of chlorinated hydrocarbons in contaminated sites.
In this research, α-FeOOH and Shewanella putrefaciens CN32 (CN32) were selected as mineral and DIRB to investigate the mechanism of EDDS enhance the bio-reduction of mineral in anaerobic environments. The objectives of this study was to characterize the generation of surface-bound Fe(II) (FeIIEDDS) during the bio-reduction of α-FeOOH by CN32 when addition of EDDS, to investigate the role of FeIIEDDS during the reductive dechlorination of chlorinated organic. Carbon tetrachloride (CT) was selected as a representative target chlorinated organic which classified as potential carcinogens and caused toxicity to human beings and ecosystems (Bae et al., 2017).
Section snippets
Chemicals
CT (>99.8%, GC grade), chloroform (CF) (>99.8%, GC grade), dichloromethane (DCM) (>98%, GC grade) and chloromethane (CM) (>98%, GC grade) were purchased from Aladdin Biochemical Technology Co. Ltd (Shanghai, China). EDTA (C10H16N2O8, 99%), EDDS (C10H16N2O8, >98%) and Sodium lactate (C3H5NaO3, 99%) were purchased from Kuer Chemical Technology Co. Ltd (Beijing, China). All the other chemicals were of analytical grade and were used as received without further purification. α-FeOOH was synthesized
EDDS enhanced bio-reduction of α-FeOOH by CN32
Bio-reduction of 10 mM α-FeOOH (0.56 g-Fe L−1) by CN32 in the presence of various concentrations EDDS or EDTA at neutral pH was characterized by measuring the concentration of dissolved Fe(II) (Fig. 1). The concentrations of Fe(II) significantly increased in the presence of various concentrations EDTA or EDDS with CN32 in 15 d, while no increase of Fe(II) was observed in the controls. The concentration of Fe(II) in α-FeOOH suspension without CN32 was low due to its slow dissolution rate and/or
Conclusion
EDDS as a new type of environmentally friendly chelating agent, have been used for contaminant degradation purposes in the recently published works, especially in removal of heavy metal ions in contaminated sites (Kowalczyk et al., 2013, Cui et al., 2017). In this study, it found that addition EDDS significantly enhanced the production of dissolved and sorbed Fe(II) after incubation due to EDDS has strong complexation abilities to combine with iron oxides. The reductive dechlorination of CT can
Acknowledgements
This work was supported jointly by the National key research and development plan (2016YFC0206200), the National Natural Science Foundation of China (51578240), the Fok Ying Tung Education Foundation (141077), Open Foundation of State Key Laboratory of Environmental Criteria and Risk Assessment Chinese Research Academy of Environmental Sciences (SKLECRA2016OFP19), Open Foundation of Shanghai Key Lab for Urban Ecological Processes and Eco-Restoration, and the Innovation Program of the Shanghai
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