Complete reductive dehalogenation of brominated biphenyls by anaerobic microorganisms in sediment.

We sought to determine whether microorganisms from the polychlorinated biphenyl (PCB)-contaminated sediment in Woods Pond (Lenox, Mass.) could dehalogenate brominated biphenyls. The PCB dechlorination specificities for the microorganisms in this sediment have been well characterized. This allowed us to compare the dehalogenation specificities for brominated biphenyls and chlorinated biphenyls within a single sediment. Anaerobic sediment microcosms were incubated separately at 25 degrees C with 16 different mono- to tetrabrominated biphenyls (350 muM) and disodium malate (10 mM). Samples were extracted and analyzed by gas chromatography with an electron capture detector and a mass spectrometer detector at various times for up to 54 weeks. All of the tested brominated biphenyls were dehalogenated. For most congeners, including 2,6-dibromobiphenyl (26-BB) and 24-25-BB, the dehalogenation began within 1 to 2 weeks. However, for 246-BB and 2-2-BB, debromination was first observed at 7 and 14 weeks, respectively. Most intermediate products did not persist, but when 2-2-BB was produced as a dehalogenation product, it persisted for at least 15 weeks before it was dehalogenated to 2-BB and then to biphenyl. The dehalogenation specificities for brominated and chlorinated biphenyls were similar: meta and para substituents were generally removed first, and ortho substituents were more recalcitrant. However, the brominated biphenyls were better dehalogenation substrates than the chlorinated biphenyls. All of the tested bromobiphenyls, including those with ortho and unflanked meta and para substituents, were ultimately dehalogenated to biphenyl, whereas their chlorinated counterparts either were not dehalogenation substrates or were only partially dehalogenated. Our data suggest that PCB-dechlorinating microorganisms may be able to dehalogenate brominated biphenyls and may exhibit a relaxed specificity for these substrates.

Temperature determines the pattern of anaerobic microbial dechlorination of Aroclor 1260 primed by 2,3,4,6-tetrachlorobiphenyl in Woods Pond sediment.

Reductive dechlorination of the Aroclor 1260 residue in Woods Pond (Lenox, Mass.) sediment samples was investigated for a year at incubation temperatures from 4 to 66 degrees C. Sediment slurries were incubated anaerobically with and without 2,3,4,6-tetrachlorobiphenyl (2346-CB; 350 microM) as a primer for dechlorination of the Aroclor 1260 residue. Dechlorination of the Aroclor residue occurred only in live samples primed with 2346-CB and only at 8 to 34 degrees C and 50 to 60 degrees C. The extent and pattern of polychlorinated biphenyl (PCB) dechlorination were temperature dependent. At 8 to 34 degrees C, the dechlorination resulted in 28 to 65% decreases of the hexathrough nonachlorobiphenyls and corresponding increases in the tri- and tetrachlorobiphenyls. At 12 to 30 degrees C, 30 to 40% of the hexa- through nonachlorobiphenyls were dechlorinated in just 3 months. The optimal temperature for overall chlorine removal was 20 to 27 degrees C. We observed four different microbial dechlorination processes with different but partially overlapping temperature ranges, i.e., Process N (flanked meta dechlorination) at 8 to 30 degrees C, Process P (flanked para dechlorination) at 12 to 34 degrees C, Process LP (unflanked para dechlorination) at 18 to 30 degrees C, and Process T (a very restricted meta dechlorination of specific hepta- and octachlorobiphenyls) at 50 to 60 degrees C. These temperature ranges should aid in the development of strategies for the enrichment and isolation of the microorganisms responsible for each dechlorination process. The incubation temperature determined the relative dominance of the four PCB dechlorination processes and the extent and products of dechlorination. Hence, understanding the effects of temperature on PCB dechlorination at contaminated sites should assist in predicting the environmental fate of PCBs or planning bioremediation strategies at those sites.

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.

Influence of incubation temperature on the microbial reductive dechlorination of 2,3,4,6-tetrachlorobiphenyl in two freshwater sediments.

Volumn 62, no. 11, p. 4174, Abstract, lines 12 and 13: "para dechlorination was restricted from 18 to 34(deg)C" should read "para dechlorination was restricted to temperatures from 18 to 34(deg)C." [This corrects the article on p. 4174 in vol. 62.].

Influence of incubation temperature on the microbial reductive dechlorination of 2,3,4,6-tetrachlorobiphenyl in two freshwater sediments.

We studied the impact of incubation temperatures on the dechlorination of 2,3,4,6-tetrachlorobiphenyl (2346-CB) in two sediments from different climates: polychlorinated biphenyl (PCB)-free sediment from Sandy Creek Nature Center Pond (SCNC) in Athens, Ga., and PCB-contaminated sediment from Woods Pond (WP) in Lenox, Mass. Sediment slurries were incubated anaerobically with 350 (mu)M 2346-CB for 1 year at temperatures ranging from 4 to 66(deg)C. Most of the 2346-CB was dechlorinated between 12 and 34(deg)C in both sediments and, unexpectedly, between 50 and 60(deg)C in WP sediment. This is the first report of PCB dechlorination at thermobiotic temperatures. The data reveal profound differences in dechlorination rate, extent, and products as a function of sediment and temperature. The highest observed rate of dechlorination of 2346-CB to trichlorobiphenyls occurred at 30(deg)C in both sediments, but the rate was higher for WP than for SCNC sediment (46 versus 16 (mu)mol liter(sup-1) day(sup-1)). For SCNC sediment the rate of dechlorination dropped sharply below 30(deg)C, but for WP sediments it was near optimal from 20 to 34(deg)C and then dropped sharply below 20(deg)C. In WP sediment most of the meta chlorines were removed between 8 and 34(deg)C and between 50 and 60(deg)C. para dechlorination was restricted from 18 to 34(deg)C and was optimal at 20(deg)C. ortho dechlorination occurred between 8 and 30(deg)C, with optima around 15 and 27(deg)C, but the extent was highly variable. In SCNC sediment complete meta dechlorination occurred from 12 to 34(deg)C and para dechlorination occurred from 18 to 30(deg)C; both were optimal at 30(deg)C. No ortho dechlorination was observed. Dechlorination products were 246-CB, 236-CB, and 26-CB (both sediments) and 24-CB, 2-CB, and 4-CB (WP sediment). The data suggest that in SCNC sediment similar factors controlled meta and para PCB dechlorination over a broad temperature range (18 to 30(deg)C) but that in WP sediment there were multiple temperature-dependent changes in the factors controlling ortho, meta, and para dechlorination. We attribute the differences observed in the two sediments to differences in their PCB-dechlorinating communities.

Aerobic degradation of polychlorinated biphenyls by Alcaligenes sp. JB1: metabolites and enzymes.

In contrast to the degradation of penta- and hexachlorobiphenyls in chemostat cultures, the metabolism of PCBs by Alcaligenes sp. JB1 was shown to be restricted to PCBs with up to four chlorine substituents in resting-cell assays. Among these, the PCB congeners containing ortho chlorine substituents on both phenyl rings were found to be least degraded. Monochloro-benzoates and dichlorobenzoates were detected as metabolites. Resting cell assays with chlorobenzoates showed that JB1 could metabolize all three monochlorobenzoates and dichlorobenzoates containing only meta and para chlorine substituents, but not dichlorobenzoates possessing an ortho chlorine substituent. In enzyme activity assays, meta cleaving 2,3-dihydroxybiphenyl 1,2-dioxygenase and catechol 2,3-dioxygenase activities were constitutive, whereas benzoate dioxygenase and ortho cleaving catechol 1,2-dioxygenase activities were induced by their substrates. No activity was found for pyrocatechase II, the enzyme that is specific for chlorocatechols. The data suggest that complete mineralization of PCBs with three or more chlorine substituents by Alcaligenes sp. JB1 is unlikely.

Reductive ortho and meta Dechlorination of a Polychlorinated Biphenyl Congener by Anaerobic Microorganisms.

We used gas chromatography-mass spectrometry to study the metabolic fate of 2,3,5,6-tetrachlorobiphenyl (2356-CB) (350 muM) incubated with unacclimated methanogenic pond sediment. The 2356-CB was dechlorinated to 25-CB (21%), 26-CB (63%), and 236-CB (16%) in 37 weeks. This is the first experimental demonstration of ortho dechlorination of a polychlorinated biphenyl by anaerobic microorganisms.

Influence of chroline substitution pattern on the degradation of polychlorinated biphenyls by eight bacterial strains.

We compared the metabolism of eight di- and trichlorobiphenyls by eight bacterial strains chosen to represent a broad range of degradative activity against polychlorinated biphenyls (PCBs). The PCB congeners used were 2,3-, 2,3'-, 2,4'-, 3,3'-, 2,3,3'-, 2,4,4'-, 2,5,3'-, and 3,4,2'-chlorobiphenyl. The bacterial strains used wereCorynebacterium sp. MB1,Alcaligenes strainsA. eutrophus H850 andA. faecalis Pi434, andPseudomonas strains LB400 and H1130,P. testosteroni H430 and H336, andP. cepacia H201. The results indicated that both the relative rates of primary degradation of PCBs and the choice of the ring attacked were dependent on the bacterial strain used. The bacterial strains exhibited considerable differences in their relative reactivity preferences for attack on mono- and dichlorophenyl groups and in the degree to which the attack was affected by the chlorine substitution pattern on the nonreacting ring. For MB1 the reactivity pattern was 3-≥4-≫2-chlorophenyl with no attack on 2,4- or 2,5-chlorophenyl groups. This strain was relatively insensitive to the chlorine substitution pattern on the nonreacting ring. Strains H1130, H430, H201, and Pi434 exhibited the same reactivity preferences as MB1, but for these strains (and for all others tested) the chlorination pattern on the nonreacting ring had a strong effect. For strain H336 the reactivity preference was 4-≥2->2,4-≥3-chlorophenyl, with no evidence of attack on 2,5-chlorophenyl rings. For strains H850 and LB400 the relative reactivity was 2->2,5->3-≫2,4->4-chlorophenyl. On this basis we propose that the eight bacterial strains represent four distinct classes of biphenyl/PCB-dioxygenase activity.The types of products formed were largely strain-independent and were determined primarily by the chlorine substitution pattern on the reacting ring. When the reacting ring was an unsubstituted phenyl or a 2-chlorophenyl group, the products were chlorobenzoic acids in high yields; for a 3-chlorophenyl ring, both chlorobenzoic acids and chloroacetophenones in moderate yields; and for a 4- or 2,4-chlorophenyl group, chlorobenzoic acids in low yields with an apparent accumulation ofmeta ring-fission product. Strains H850 and LB400 were able to degrade the 3-chlorobenzoic acid that they produced from the degradation of 2,3'-chlorobiphenyl. We conclude that despite differences among strains in the specificity of the initial dioxygenase, the specificities of the enzymes responsible for the subsequent degradation to chlorobenzoic acid and/or chloroacetophenone are quite similar for all strains.

Polychlorinated biphenyl dechlorination in aquatic sediments.

The polychlorinated biphenyl (PCB) residues in the aquatic sediments from six PCB spill sites showed changes in PCB isomer and homolog (congener) distribution that indicated the occurrence of reductive dechlorination. The PCB dechlorinations exhibited several distinct congener selection patterns that indicated mediation by several different localized populations of anaerobic microorganisms. The higher (more heavily chlorinated) PCB congeners that were preferentially attacked by the observed dechlorination processes included all those that are either pharmacologically active or persistent in higher animals. All the lower (less heavily chlorinated) PCB congeners formed by the dechlorinations were species that are known to be oxidatively biodegradable by the bacteria of aerobic environments.

Extensive degradation of Aroclors and environmentally transformed polychlorinated biphenyls by Alcaligenes eutrophus H850.

We have isolated and characterized a strain of Alcaligenes eurtrophus, designated H850, that rapidly degrades a broad and unusual spectrum of polychlorinated biphenyls (PCBs) including many tetra- and pentachlorobiphenyls and several hexachlorobiphenyls. This strain, which was isolated from PCB-containing dredge spoils by enrichment on biphenyl, grows well on biphenyl and 2-chlorobiphenyl but poorly on 3- and 4-chlorobiphenyl. Capillary gas-chromatographic analysis showed that biphenyl-grown resting cells of H850 degraded the components of 38 of the 41 largest peaks of Aroclor 1242 and 15 of the 44 largest peaks of Aroclor 1254, resulting in an overall reduction of PCBs by 81% for Aroclor 1242 (10 ppm) and 35% for Aroclor 1254 (10 ppm) in 2 days. Furthermore, H850 metabolized the predominantly ortho-substituted PCB congeners that resulted from the environmental transformation of the more highly chlorinated congeners of Aroclor 1242 by the upper Hudson River anaerobic meta-, para-dechlorination agent system C (J. F. Brown, R. E. Wagner, Jr., D. L. Bedard, M. J. Brennan, J. C. Carnahan, R. J. May, and J. J. Tofflemire, Northeast Environ. Sci. 3:167-179, 1984). The congener selectivity patterns indicate that a two-step process consisting of anaerobic dechlorination followed by oxidation by H850 can effectively degrade all of the congeners in Aroclor 1242 and possibly all those in Aroclor 1254.

Evidence for novel mechanisms of polychlorinated biphenyl metabolism in Alcaligenes eutrophus H850.

Previous studies indicated that Alcaligenes eutrophus H850 attacks a different spectrum of polychlorinated biphenyl (PCB) congeners than do most PCB-degrading bacteria and that novel mechanisms of PCB degradation might be involved. To delineate this, we have investigated the differences in congener selectivity and metabolite production between H850 and Corynebacterium sp. strain MB1, an organism that apparently degrades PCBs via a 2,3-dioxygenase. H850 exhibited a superior ability to degrade congeners via attack on 2-, 2,4-, 2,5-, or 2,4,5-chlorophenyl rings in PCBs but an inferior ability to degrade congeners via attack on a 4-chlorophenyl ring. Reactivity preferences were also reflected in the products formed from unsymmetrical PCBs; thus MB1 attacked the 2,3-chlorophenyl ring of 2,3,2',5'-tetrachlorobiphenyl to yield 2,5-dichlorobenzoic acid, while H850 attacked the 2,5-chlorophenyl ring to yield 2,3-dichlorobenzoic acid and a novel metabolite, 2',3'-dichloroacetophenone. Furthermore, H850 oxidized 2,4,5,2',4',5'-hexachlorobiphenyl, a congener with no adjacent unsubstituted carbons, to 2',4',5'-trichloroacetophenone. The atypical congener selectivity pattern and novel metabolites produced suggest that A. eutrophus H850 may degrade certain PCB congeners by a new route beginning with attack by some enzyme other than the usual 2,3-dioxygenase.

Rapid assay for screening and characterizing microorganisms for the ability to degrade polychlorinated biphenyls.

We designed a rapid assay that assesses the polychlorinated biphenyl (PCB)-degradative competence and congener specificity of aerobic microorganisms, identifies strains capable of degrading highly chlorinated biphenyls, and distinguishes among those that degrade PCBs by alternative pathways. Prior attempts to assay PCB-degradative competence by measuring disappearance of Aroclors (commercial PCB mixtures) have frequently produced false-positive findings because of volatilization, adsorption, or absorption losses. Furthermore, these assays have generally left the chemical nature of the competence obscure because of incomplete gas chromatographic resolution and uncertain identification of Aroclor peaks. We avoided these problems by using defined mixtures of PCB congeners and by adopting incubation and extraction methods that prevent physical loss of PCBs. Our assay mixtures include PCB congeners ranging from dichloro- to hexachlorobiphenyls and representing various structural classes, e.g., congeners chlorinated on a single ring (2,3-dichlorobiphenyl), blocked at 2,3 sites (2,5,2'5'-tetrachlorobiphenyl), blocked at 3,4 sites (4,4'-dichlorobiphenyl), and lacking adjacent unchlorinated sites (2,4,5,2',4',5'-hexachlorobiphenyl). The PCB-degrative ability of microorganisms is assessed by packed-column gas chromatographic analysis of these defined congener mixtures following 24-h incubation with resting cells. When tested with 25 environmental isolates, this assay revealed a broad range of PCB-degradative competence, highlighted differences in congener specificity and in the extent of degradation of individual congeners, predicted degradative competence on commercial PCBs, and (iv) identified strains with superior PCB-degradative ability.

Structural proteins and cell-free translation products of total RNA and hybrid-selected RNA from two DNA variants of vaccinia virus.

Two major variants of vaccinia virus, large (L) and small (S), differ by a deletion of 9.7 kilobase pairs. The structural proteins and the translation products of RNA transcribed in vitro from each of these variants were analyzed by gel electrophoresis. Recombinant plasmids were used to select RNA transcribed from the L variant sequences corresponding to the deletion. This RNA yielded translation products indicating that a minimum of 11 polypeptides, including two structural proteins, map within the deletion.

Initiation and translation in vitro of mRNA for MOPC 315 immunoglobulin heavy chain and characterization of translation product.

An initiation study of mineral oil-induced plasmacytoma (MOPC) 315 heavy chain immunoglobulin (H315) in vitro has been conducted using formyl-[35S]methionyl-tRNAfMet and a highly purified 18 S message from MOPC 315 solid tumor in a crude rabbit reticulocyte lysate system. The product was specifically precipitated by antibodies directed against MOPC 315 immunoglobulin and H315. The in vitro H315 products terminally labeled with formyl-[35S]methionine or internally labeled with [3H]leucine were electrophoretically identical with in vivo H315 on sodium dodecyl sulfate-polyacrylamide gels. All of the [35S]-methionine was incorporated at the NH2 terminus, not internally, since there is a near complete recovery of [35S]methionine following one cycle of Edman degradation. The NH2-terminal cyanogen bromide peptide, CN2, of in vivo and in vitro H315 co-migrated exactly on gel electrophoresis under conditions which completely resolved two proteins differing in size by only 14 amino acids. These data strongly suggest that there is no NH2-terminal precursor of H315 in this system. Cyanogen bromide peptide profiles of in vivo and in vitro H315 were chromatographically indistinguishable. Three peptides, CN1, CN2, and CN4, which represent approximately 85% of the total amino acids of H315 were isolated and further characterized by electrophoresis and paper chromatography. All were very similar to the corresponding peptides of authentic H315. We conclude that the fidelity of H315 translation is preserved in vitro.