Evidence for para dechlorination of polychlorobiphenyls by methanogenic bacteria

Waste activated sludge stimulates in situ microbial reductive dehalogenation of organohalide-contaminated soil

Due to its enriched organic matter, nutrients and growth cofactors, as well as a diverse range of microorganisms, waste activated sludge (WAS) might be an ideal additive to stimulate organohalide respiration for in situ bioremediation of organohalide-contaminated sites. In this study, we investigated the biostimulation and bioaugmentation impacts of WAS-amendment on the performance and microbiome in tetrachloroethene (PCE) and polychlorinated biphenyls (PCBs) dechlorinating microcosms. Results demonstrated that WAS-amendment increased PCE- and PCBs-dechlorination rate as much as 6.06 and 10.67 folds, respectively. The presence of WAS provided a favorable growth niche for organohalide-respiring bacteria (OHRB), including redox mediation and generation of electron donors and carbon sources. Particularly for the PCE dechlorination, indigenous Geobacter and WAS-derived Dehalococcoides were identified to play key roles in PCE-to-dichloroethene (DCE) and DCE-to-ethene dechlorination, respectively. Similar biostimulation and bioaugmentation effects of WAS-amendment were observed on both PCE- and PCBs-dechlorination in three different soils, i.e., laterite, brown loam and paddy soil. Risk assessment suggested low potential ecological risk of WAS amendment in remediation of organohalide-contaminated soil. Overall, this study provided an economic and efficient strategy to stimulate the organohalide respiration-based bioremediation in field applications.

Microbial synergistic interactions for reductive dechlorination of polychlorinated biphenyls

Dehalococcoides usually work closely with other beneficial microorganisms for removal of halogenated organic compounds at contaminated sites. Traditional microbial cultivation is necessary but not enough to gain insights into key microbial populations and their interactions in complex communities. In this study, we cultivated and characterized two D. mccartyi strains (CG3 and SG1), and further revealed interspecies synergistic interactions in PCB-dechlorinating microbial communities via metagenomic analysis. Strain CG3 and SG1 originated from distinct geographic sites employ reductive dehalogenase CG3-RD11 (PcbA1-like) and SG1-RD28 (PcbA4/5-like), respectively, to catalyze chlorine-removal from PCBs. In their parent mixed cultures CG-3 and SG-1, as well as in previously enriched PCB-dechlorinating cultures CG-1, CG-4 and CG-5, Methanosarcina and Desulfovibrio were found as major non-dechlorinating populations which may play roles in mediating acetate- and H₂-sources for D. mccartyi. They together form a stable microbial community for interspecies carbon- and electron-transfers to facilitate organohalide respiration of D. mccartyi, being confirmed in a synthetic microbial community consisting of the Dehalococcoides, Methanosarcina and Desulfovibrio. The results provide insights into which and how other microorganisms support D. mccartyi to dechlorinate PCBs, and suggest that Methanosarcina may play a larger role in PCB-dechlorinating communities than currently appreciated.

Indirect Evidence Link PCB Dehalogenation with Geobacteraceae in Anaerobic Sediment-Free Microcosms

Although polychlorinated biphenyls (PCBs) production was brought to a halt 30 years ago, recalcitrance to degradation makes them a major environmental pollutant at a global scale. Previous studies confirmed that organohalide-respiring bacteria (OHRB) were capable of utilizing chlorinated congeners as electron acceptor. OHRB belonging to the Phyla Chloroflexi and Firmicutes are nowadays considered as the main PCB-dechlorinating organisms. In this study, we aimed at exploring the involvement of other taxa in PCB dechlorination using sediment-free microcosms (SFMs) and the Delor PCB mixture. High rates of congener dehalogenation (up to 96%) were attained in long-term incubations of up to 692 days. Bacterial communities were dominated by Chloroflexi, Proteobacteria, and Firmicutes, among strictly simplified community structures composed of 12 major phyla only. In a first batch of SFMs, Dehalococcoides mccartyi closely affiliated with strains CG4 and CBDB1 was considered as the main actor associated with congener dehalogenation. Addition of 2-bromoethanesulfonate (BES), a known inhibitor of methanogenic activity in a second batch of SFMs had an adverse effect on the abundance of Dehalococcoides sp. Only two sequences affiliated to this Genus could be detected in two (out of six) BES-treated SFMs, contributing to a mere 0.04% of the communities. BES-treated SFMs showed very different community structures, especially in the contributions of organisms involved in fermentation and syntrophic activities. Indirect evidence provided by both statistical and phylogenetic analysis validated the implication of a new cluster of actors, distantly affiliated with the Family Geobacteraceae (Phylum δ-Proteobacteria), in the dehalogenation of low chlorinated PCB congeners. Members of this Family are known already for their dehalogenation capacity of chlorinated solvents. As a result, the present study widens the knowledge for the phylogenetic reservoir of indigenous PCB dechlorinating taxa.

Dynamics of brominated flame retardants removal in contaminated wastewater sewage sludge under anaerobic conditions

Disposal of solid waste to landfills from waste water sewage treatment plants (WWTPs) serves as a potential source of contamination by polybrominated diphenyl ethers (PBDEs) and hexabromocyclododecane (HBCD). Native microbial communities have been found to degrade a variety of xenobiotics, such as PBDEs and HBCDs. This study investigates the potential of autochthonous microflora to remove 11 PBDE congeners and HBCDs in waste water sludge under anaerobic conditions. Laboratory microcosms were constructed with sewage sludge from the WWTPs of Hradec Kralove and Brno. BDE 209 was detected as the prevailing congener in concentrations 685 and 1403 ng/g dw and the total amounts of 10 lower PBDEs (BDE 28, 47, 49, 66, 85, 99, 100, 153, 154, 183) were 605 and 205 ng/g dw in sludge from Hradec Kralove and Brno, respectively. The levels of HBCD were detected in both sludge lower than 24 ng/g dw. The experiment was carried out for 15 months. After three months of incubation, HBCD was completely degraded to below detection limits. In sewage from both WWTPs, the higher brominated DEs were removed faster than the lower brominated congeners. One exception was tri-BDE, which was degraded completely within 15 months of cultivation. A significant increase in congener tetra-BDE 49 concentrations was observed over the course of the experiment in all tested sewage. The relative distribution of individual congeners among all PBDEs changed after 15 months of the incubation in favour of lower brominated congeners. This indicates that debromination is the major mechanism of anaerobic biodegradation. Despite of the increase of BDE 49, the overall removal of all 11 PBDEs achieved the levels of 47.4 and 68.7% in samples from WWTPs Hradec Kralove and Brno, respectively.

Overview of in situ and ex situ remediation technologies for PCB-contaminated soils and sediments and obstacles for full-scale application

Polychlorinated biphenyls (PCB) are persistent organic pollutants used worldwide between the 1930s and 1980s. Although their use has been heavily restricted, PCB can be found in contaminated soils and sediments. The most frequent remediation solutions adopted are "dig and dump" and "dig and incinerate", but there are currently new methods that could be more sustainable alternatives. This paper takes a look into the remediation options available for PCB-contaminated soils and sediments, differentiating between biological, chemical, physical and thermal methods. The use of combined technologies was also reviewed. Most of them are still in an initial development stage and further research in different implementation issues is needed. There is no single technology that is the solution for PCB contamination problem. The successful remediation of a site will depend on proper selection, design and adjustment of the technology or combined technologies to the site characteristics.

Enrichment and properties of a 1,2,4-trichlorobenzene-dechlorinating methanogenic microbial consortium

A methanogenic microbial consortium capable of reductively dechlorinating 1,2,4-trichlorobenzene (1,2,4-TCB) was enriched from a mixture of polluted sediments. 1,2,4-TCB was dechlorinated via 1,4-dichlorobenzene (1,4-DCB) to chlorobenzene (CB). Lactate, which was used as an electron donor during the enrichment, was converted via propionate and acetate to methane. Glucose, ethanol, methanol, propionate, acetate, and hydrogen were also suitable electron donors for dechlorination, whereas formate was not. The addition of 5% (wt/vol) sterile Rhine River sand was necessary to maintain the dechlorinating activity of the consortium. The addition of 2-bromoethanesulfonic acid (BrES) inhibited methanogenesis completely but had no effect on the dechlorination of 1,2,4-TCB. The consortium was also able to dechlorinate other chlorinated benzenes via various simultaneous pathways to 1,3,5-TCB, 1,2-DCB, 1,3-DCB, or CB as an end product. The addition of BrES inhibited several of the simultaneously occurring dechlorination pathways of 1,2,3,4- and 1,2,3,5-tetrachlorobenzene and of pentachlorobenzene, which resulted in the formation of CB as the only final product. Hexachlorobenzene and polychlorinated biphenyls (PCBs) were dechlorinated after a lag phase of ca. 15 days, showing a dechlorination pattern that is different from those observed for lower chlorinated benzenes: only chlorines with two adjacent chlorines were removed. The results show that the consortium possesses at least three distinct dechlorination activities toward chlorinated benzenes and PCBs.

A case study for microbial biodegradation: anaerobic bacterial reductive dechlorination of polychlorinated biphenyls-from sediment to defined medium

The history of anaerobic microbial polychlorinated biphenyl (PCB) dechlorination is traced over 20 years using a case study of PCB dechlorination in the Housatonic River (Massachusetts) as an example. The history progresses from the characterization of the PCBs in the sediment, to cultivation in sediment microcosms, to the identification of four distinct types of PCB dechlorination, to a successful field test, to the cultivation in defined medium of the organisms responsible for extensive dechlorination of Aroclor 1260, and finally to the identification of a Dehalococcoides population that links its growth to the dechlorination of Aroclor 1260. Other PCB dechlorinators have also been identified. Two bacterial strains, o-17 and DF-1, that link their growth to the dechlorination of several PCB congeners belong to a novel clade of putative dechlorinating bacteria within the phylum Chloroflexi. Dehalococcoides ethenogenes strain 195 also dechlorinates several PCB congeners when grown on chlorinated ethenes. Evidence is mounting that Dehalococcoides and other dechlorinating Chloroflexi may play a significant role in the dechlorination of commercial PCBs in situ.

Enrichment of anaerobic polychlorinated biphenyl dechlorinators from sediment with iron as a hydrogen source

Little is known about anaerobic polychlorinated biphenyl (PCB) dechlorination, although it is believed that some microorganisms are capable of respiring PCBs, gaining energy for growth from PCB dechlorination. If this is the case, the amendment of appropriate electron donors to contaminated sediment should stimulate dechlorination. The effect of elemental iron (Fe0) addition, an easily amended electron donor, on the microbial dechlorination of the PCB congeners 3,4,5-trichlorobiphenyl (3,4,5-CB) and 2,2',3,4,4',5,5'-heptachlorobiphenyl (2,2',3,4,4',5,5'-CB) was investigated in microcosms containing estuarine sediment from Baltimore Harbor. Results showed that the addition of 0.1 g Fe0/g sediment reduced the lag time for removal of doubly flanked para chlorines by approximately 100 days. Because Fe0 is a source of cathodic hydrogen (H2), the effect of direct H2 addition to sediment microcosms was also tested. The addition of 0.001 atm H2 in the headspace generated the same dechlorination activity and reduction in lag time as the addition of 0.1g Fe0/g. Higher concentrations of Fe0 or H2 increased the lag prior to dechlorination. Additional results showed that an alkaline pH (> or = 7.5), high [Fe2+] (3.3 g/L), or HS- (0.1 mg/L total sulfide) inhibited dechlorination. Elevated concentrations of Fe2+, OH-, and HS- are products of Fe0 oxidation or increased microbial activity (methanogenesis, homoacetogenesis, and sulfate reduction), both of which would result from the amendment of large quantities of Fe0 or H2 to sediment. This research shows that not only can PCB dechlorination be stimulated through the addition of electron donor, but implies that the dechlorinators are enriched by the continuous addition of low concentrations of H2, similar to other known dechlorinators, such as the dehalorespirer Dehalococcoides ethenogenes. These results suggest that the direct addition of controlled amounts of Fe0 to sediments may be an effective remediation tool to reduce the lag period prior to dechlorination at PCB-impacted sites. They also suggest that PCB dechlorinators may be enriched using techniques similar to those used with known dehalorespirers.

Potential for anaerobic conversion of xenobiotics

This review covers the latest research on the anaerobic biodegradation of aromatic xenobiotic compounds, with emphasis on surfactants, polycyclic aromatic hydrocarbons, phthalate esters, polychlorinated biphenyls, halogenated phenols, and pesticides. The versatility of anaerobic reactor systems regarding the treatment of xenobiotics is shown with the focus on the UASB reactor, but the applicability of other reactor designs for treatment of hazardous waste is also included. Bioaugmentation has proved to be a viable technique to enhance a specific activity in anaerobic reactors and recent research on reactor and in situ bioaugmentation is reported.

Dechlorination pathways of ortho-substituted PCBs by UV irradiation in n-hexane and their correlation to the charge distribution on carbon atom

The photodegradations of 22 individual polychlorinated biphenyl (PCB) congeners (including 21 non-coplanar ortho substituted and one non-ortho substituted) by irradiation with ultraviolet lamp in n-hexane solution were studied. Photoproducts were identified by matching their retention times and mass spectra with those of authentic standards. PCB congener with less than two chlorides was photodegraded within half an hour, if more than three chlorine on ring, the photodechlorination time for PCB needs one and half hours or more, sometimes even longer than 15 h. The half-life of PCB degradation by photodechlorination was much shorter than that by anaerobic biological dechlorination. Charge distribution on carbon atom combined with the monitoring products of individual PCB congeners were used to deduce the photodegradation pathways. The higher the charge distribution for carbon to which chlorine is attached, the easier for photodechlorination to occur. A lot of chlorine atoms attached PCB, the dechlorination was found to occur prior to the carbon with higher charge distribution at the benzene ring with more chlorine atoms attached.

Microbial growth on dichlorobiphenyls chlorinated on both rings as a sole carbon and energy source

We have isolated bacterial strains capable of aerobic growth on ortho-substituted dichlorobiphenyls as sole carbon and energy sources. During growth on 2,2'-dichlorobiphenyl and 2,4'-dichlorobiphenyl strain SK-4 produced stoichiometric amounts of 2-chlorobenzoate and 4-chlorobenzoate, respectively. Chlorobenzoates were not produced when strain SK-3 was grown on 2,4'-dichlorobiphenyl.

Microbial reductive dehalogenation of polychlorinated biphenyls

Under anaerobic conditions, microbial reductive dechlorination of polychlorinated biphenyls (PCBs) occurs in soils and aquatic sediments. In contrast to dechlorination of supplemented single congeners for which frequently ortho dechlorination has been observed, reductive dechlorination mainly attacks meta and/or para chlorines of PCB mixtures in contaminated sediments, although in a few instances ortho dechlorination of PCBs has been observed. Different microorganisms appear to be responsible for different dechlorination activities and the occurrence of various dehalogenation routes. No axenic cultures of an anaerobic microorganism have been obtained so far. Most probable number determinations indicate that the addition of PCB congeners, as potential electron acceptors, stimulates the growth of PCB-dechlorinating microorganisms. A few PCB-dechlorinating enrichment cultures have been obtained and partially characterized. Temperature, pH, availability of naturally occurring or of supplemented carbon sources, and the presence or absence of H(2) or other electron donors and competing electron acceptors influence the dechlorination rate, extent and route of PCB dechlorination. We conclude from the sum of the experimental data that these factors influence apparently the composition of the active microbial community and thus the routes, the rates and the extent of the dehalogenation. The observed effects are due to the specificity of the dehalogenating bacteria which become active as well as changing interactions between the dehalogenating and non-dehalogenating bacteria. Important interactions include the induced changes in the formation and utilization of H(2) by non-dechlorinating and dechlorinating bacteria, competition for substrates and other electron donors and acceptors, and changes in the formation of acidic fermentation products by heterotrophic and autotrophic acidogenic bacteria leading to changes in the pH of the sediments.

Establishment of a polychlorinated biphenyl-dechlorinating microbial consortium, specific for doubly flanked chlorines, in a defined, sediment-free medium

Estuarine sediment from Charleston Harbor, South Carolina, was used as inoculum for the development of an anaerobic enrichment culture that specifically dechlorinates doubly flanked chlorines (i.e., chlorines bound to carbon that are flanked on both sides by other chlorine-carbon bonds) of polychlorinated biphenyls (PCBs). Dechlorination was restricted to the para chlorine in cultures enriched with 10 mM fumarate, 50 ppm (173 microM) 2,3,4, 5-tetrachlorobiphenyl, and no sediment. Initially the rate of dechlorination decreased upon the removal of sediment from the medium. However, the dechlorinating activity was sustainable, and following sequential transfer in a defined, sediment-free estuarine medium, the activity increased to levels near that observed with sediment. The culture was nonmethanogenic, and molybdate, ampicillin, chloramphenicol, neomycin, and streptomycin inhibited dechlorination activity; bromoethanesulfonate and vancomycin did not. Addition of 17 PCB congeners indicated that the culture specifically removes double flanked chlorines, preferably in the para position, and does not attack ortho chlorines. This is the first microbial consortium shown to para or meta dechlorinate a PCB congener in a defined sediment-free medium. It is the second PCB-dechlorinating enrichment culture to be sustained in the absence of sediment, but its dechlorinating capabilities are entirely different from those of the other sediment-free PCB-dechlorinating culture, an ortho-dechlorinating consortium, and do not match any previously published Aroclor-dechlorinating patterns.

2-Bromoethanesulfonate, sulfate, molybdate, and ethanesulfonate inhibit anaerobic dechlorination of polychlorobiphenyls by pasteurized microorganisms

Dechlorination of Aroclor 1242 by pasteurized microorganisms was inhibited by 2-bromoethanesulfonate (BES), sulfate, molybdate, and ethanesulfonate. Consumption of these anions and production of sulfide from BES were detected. The inhibition could not be relieved by hydrogen. Taken together these results suggest that pattern M dechlorination is mediated by spore-forming sulfidogenic bacteria. These results also suggest that BES may inhibit anaerobic dechlorination by nonmethanogens by more than one mechanism.

Effect of Specific Inhibitors on the Anaerobic Reductive Dechlorination of 2,4,6-Trichlorophenol by a Stable Methanogenic Consortium

The transformation of 2,4,6-trichlorophenol (TCP) into 4-chlorophenol (4CP) was studied using a stable methanogenic enrichment culture derived from an anaerobic fixed bed reactor. Using acetate as a growth substrate, different inhibitors of methanogenesis exhibited distinct effects on TCP dechlorination. Whereas reductive dechlorination activity was not affected by 2% ethylene in the gas phase, 25 mM bromoethanesulfonic acid (BESA) had a direct inhibitory effect on this process. The choice of BESA as a specific inhibitor for identifying the subpopulations involved in reductive dechlorination of chloroaromatics is thus questionable. Inhibitors of sulfate reduction such as molybdate (20 mM) and selenate (20 mM) had a direct inhibitory effect on reductive dechlorination independently of the presence of sulfate in the medium supplemented with acetate as growth substrate. Consequently much more care must also be taken with these inhibitors to prove that reductive chlorination is coupled to sulfate reduction.

Two anaerobic polychlorinated biphenyl-dehalogenating enrichments that exhibit different para-dechlorination specificities

Two anaerobic polychlorinated biphenyl (PCB)-dechlorinating enrichments with distinct substrate specificities were obtained: a 2,3,4,6-tetrachlorobiphenyl (2346-CB) para-dechlorinating enrichment derived from Aroclor 1260-contaminated Woods Pond (Lenox, Mass.) sediment and a 2,4,6-trichlorobiphenyl (246-CB) unflanked para-dechlorinating enrichment derived from PCB-free Sandy Creek Nature Center (Athens, Ga.) sediment. The enrichments have been successfully transferred to autoclaved soil slurries over 20 times by using 300 to 350 microM 2346-CB or 246-CB. Both enrichments required soil for successful transfer of dechlorination activity. The 2346-CB enrichment para dehalogenated, in the absence or presence of 2346-CB, only 4 of 25 tested para halogen-containing congeners: 234-CB, 2345-CB, 2346-CB, and 2,4,6-tribromobiphenyl (246-BrB). In the presence of 246-CB, the 246-CB enrichment para dehalogenated 23 of the 25 tested congeners. However, only three congeners (34-CB, 2346-CB, and 246-BrB) were dehalogenated in the absence of 246-CB, indicating that these specific congeners initiate dehalogenation in this enrichment culture. The addition of the 2346-CB (para)-dechlorinating enrichment did not further stimulate the 2346-CB-primed dechlorination of the Aroclor 1260 residue in Woods Pond sediment samples. Compared to the addition of the primer 246-CB or the 246-CB unflanked para-dechlorinating enrichment alone, the addition of both 246-CB (300 microM) and the 246-CB enrichment stimulated the unflanked para dechlorination of the Aroclor 1260 residue in Woods Pond sediments. These results indicate that the two enrichments contain different PCB-dechlorinating organisms, each with high substrate specificities. Furthermore, bioaugmentation with the enrichment alone did not stimulate the desired dechlorination in PCB-contaminated Woods Pond sediment.

Effect of Incubation Temperature on the Route of Microbial Reductive Dechlorination of 2,3,4,6-Tetrachlorobiphenyl in Polychlorinated Biphenyl (PCB)-Contaminated and PCB-Free Freshwater Sediments

We studied the influence of temperature (4 to 66(deg)C) on the microbial dechlorination of 2,3,4,6-tetrachlorobiphenyl (2,3,4,6-CB) incubated for 1 year in anaerobic sediments from Woods Pond in Lenox, Mass., and Sandy Creek Nature Center Pond (SCNC) in Athens, Ga. Seven discrete dechlorination reactions were observed, four of which occurred in both sediments. These were 2,3,4,6-CB (symbl) 2,4,6-CB, 2,3,4,6-CB (symbl) 2,3,6-CB, 2,4,6-CB (symbl) 2,6-CB, and 2,3,6-CB (symbl) 2,6-CB. Three additional reactions occurred only in Woods Pond sediment. These were 2,4,6-CB (symbl) 2,4-CB, 2,4-CB (symbl) 2-CB, and 2,4-CB (symbl) 4-CB. The dechlorination reactions exhibited at least four different temperature dependencies in SCNC sediment and at least six in Woods Pond sediment. We attribute the discrete dechlorination reactions to different polychlorinated biphenyl (PCB)-dechlorinating microorganisms with distinct specificities. Temperature influenced the timing and the relative predominance of parallel pathways of dechlorination, i.e., meta versus para dechlorination of 2,3,4,6-CB and ortho versus para dechlorination of 2,4,6-CB and 2,4-CB. meta dechlorination of 2,3,4,6-CB to 2,4,6-CB dominated at all tested temperatures except at 18 and 34(deg)C, where para dechlorination to 2,3,6-CB dominated in some replicates. The dechlorination of 2,4,6-CB was restricted to (symbl)15 to 30(deg)C in both sediments. Temperature affected the lag time preceding the dechlorination of 2,4,6-CB in both sediments and affected the preferred route of its dechlorination in Woods Pond sediment. para dechlorination dominated at 20(deg)C, and ortho dechlorination dominated at 15(deg)C, but at 18 and 22 to 30(deg)C the relative dominance of ortho versus para dechlorination of 2,4,6-CB varied. These data indicate that field temperatures play a significant role in controlling the nature and the extent of the PCB dechlorination that occurs at a given site.

Population dynamics of polychlorinated biphenyl-dechlorinating microorganisms in contaminated sediments

The growth dynamics of polychlorinated biphenyl (PCB)-dechlorinating microorganisms were determined for the first time, along with those of sulfate reducers and methanogens, by using the most-probable-number technique. The time course of Aroclor 1248 dechlorination mirrored the growth of dechlorinators; dechlorination ensued when the dechlorinating population increased by 2 orders of magnitude from 2.5 x 10(sup5) to 4.6 x 10(sup7) cells g of sediment(sup-1), at a specific growth rate of 6.7 day(sup-1) between 2 and 6 weeks. During this period, PCB-dechlorinating microorganisms dechlorinated Aroclor 1248 at a rate of 3.9 x 10(sup-8) mol of Cl g of sediment(sup-1) day(sup-1), reducing the average number of Cl molecules per biphenyl from 3.9 to 2.8. The growth yield was 4.2 x 10(sup13) cells mol of Cl dechlorinated(sup-1). Once dechlorination reached a plateau, after 6 weeks, the number of dechlorinators began to decrease. On the other hand, dechlorinators inoculated into PCB-free sediments decreased over time from their initial level, suggesting that PCBs are required for their selective enrichment. The numbers of sulfate reducers and methanogens increased in both PCB-free and contaminated sediments, showing little difference between them. The maximum population size of sulfate reducers was about an order of magnitude higher than that of dechlorinators, whereas that of methanogens was slightly less. Unlike those of dechlorinators, however, numbers of both sulfate reducers and methanogens remained high even when dechlorination ceased. The results of this study imply that PCB concentrations may have to exceed a certain threshold to maintain the growth of PCB dechlorinators.

Microbial dechlorination of historically present and freshly spiked chlorinated dioxins and diversity of dioxin-dechlorinating populations

The ability of a microbial consortium eluted from dioxin-contaminated Passaic River sediments to dechlorinate polychlorinated dibenzo-p-dioxins (PCDDs) was investigated under methanogenic conditions. Aged 2,3,7,8-tetraCDD, which had partitioned into the microbial consortium from sediments, was stoichiometrically converted to tri- and monoCDD congeners. During dechlorination, dominant microbial activity within the consortium shifted from methanogenic to nonmethanogenic activity. Freshly spiked octaCDD was converted to hepta-, hexa-, penta-, tetra-, tri-, di-, and monochlorinated isomers, but the reaction stoichiometry was not determined. No methanogenic activity was observed, and the maximum yield of protein coincided with the production of less-chlorinated DD congeners. Two distinct pathways of dechlorination were observed: the peri-dechlorination pathway of 2,3,7,8-substituted hepta- to pentaCDDs, resulting in the production of 2,3,7,8-tetraCDD, and the peri-lateral dechlorination pathway of non-2,3,7,8-substituted congeners. Direct evidence of further lateral dechlorination of 2,3,7,8-tetraCDD was obtained from the historically contaminated incubations; no isomer-specific identification of triCDDs in spiked incubations was determined. Pasteurized cells exhibited no peri-dechlorination pathway, and triCDDs were the least-chlorinated congeners produced in these treatments. These results demonstrate that (i) both freshly spiked and aged PCDDs are available to microbial reductive dechlorination, (ii) the peri and triCDD dechlorinations are attributed to activities of nonmethanogenic, non-spore-forming microbial subpopulations, and (iii) the 2,3,7,8-residue patterns in historically contaminated sediments are likely affected by microbial activity.