Degradation of 2,4,5-trichlorophenol by the lignin-degrading basidiomycete Phanerochaete chrysosporium.

Under secondary metabolic conditions the white rot basidiomycete Phanerochaete chrysosporium rapidly mineralizes 2,4,5-trichlorophenol. The pathway for degradation of 2,4,5-trichlorophenol was elucidated by the characterization of fungal metabolites and oxidation products generated by purified lignin peroxidase (LiP) and manganese peroxidase (MnP). The multistep pathway involves cycles of peroxidase-catalyzed oxidative dechlorination reactions followed by quinone reduction reactions to yield the key intermediate 1,2,4,5-tetrahydroxybenzene, which is presumably ring cleaved. In the first step of the pathway, 2,4,5-trichlorophenol is oxidized to 2,5-dichloro-1,4-benzoquinone by either MnP or Lip. 2,5-Dichloro-1,4-benzoquinone is then reduced to 2,5-dichloro-1,4-hydroquinone. The 2,5-dichloro-1,4-hydroquinone is oxidized by MnP to generate 5-chloro-4-hydroxy-1,2-benzoquinone. The orthoquinone is in turn reduced to 5-chloro-1,2,4-trihydroxybenzene. Finally, the 5-chlorotrihydroxybenzene undergoes another cycle of oxidative dechlorination and reduction reactions to generate 1,2,4,5-tetrahydroxybenzene. The latter is presumably ring cleaved, with subsequent degradation to CO2. In this pathway, the substrate is oxidatively dechlorinated by LiP or MnP in a reaction which produces a quinone. The quinone intermediate is recycled by a reduction reaction to regenerate an intermediate which is again a substrate for peroxidase-catalyzed oxidative dechlorination. This pathway apparently results in the removal of all three chlorine atoms before ring cleavage occurs.     

Complete dechlorination of tetrachlorohydroquinone by cell extracts of pentachlorophenol-induced Rhodococcus chlorophenolicus.

In this paper we describe the sequence of reactions leading from tetrachloro-para-hydroquinone to 1,2,4-trihydroxybenzene by inducible enzymes of Rhodococcus chlorophenolicus. Tetrachlorohydroquinone was first converted to a dichlorotrihydroxybenzene in a reaction involving both hydrolytic and reductive dechlorination; no trichlorinated intermediate was detected. Dichlorotrihydroxybenzene was subsequently reductively dechlorinated to a monochlorotrihydroxybenzene and finally to 1,2,4-trihydroxybenzene. The cell extract also catalyzed, at a lower rate, reductive dechlorination of trichlorohydroquinone, mainly to 2,3-dichlorohydroquinone. To our knowledge this is the first demonstration of reductive aromatic dechlorination by bacterial enzymes.     

Degradation of 2,7-dichlorodibenzo-p-dioxin by the lignin-degrading basidiomycete Phanerochaete chrysosporium.

Under secondary metabolic conditions, the white-rot basidiomycete Phanerochaete chrysosporium degraded 2,7-dichlorodibenzo-p-dioxin (I). The pathway for the degradation of I was elucidated by the characterization of fungal metabolites and oxidation products generated by lignin peroxidase (LiP), manganese peroxidase (MnP), and crude intracellular cell-free extracts. The multistep pathway involves the degradation of I and subsequent intermediates by oxidation, reduction, and methylation reactions to yield the key intermediate 1,2,4-trihydroxybenzene (III). In the first step, the oxidative cleavage of the dioxin ring of I, catalyzed by LiP, generates 4-chloro-1,2-benzoquinone (V), 2-hydroxy-1,4-benzoquinone (VIII), and chloride. The intermediate V is then reduced to 1-chloro-3,4-dihydroxybenzene (II), and the latter is methylated to form 1-chloro-3,4-dimethoxybenzene (VI). VI in turn is oxidized by LiP to generate chloride and 2-methoxy-1,4-benzoquinone (VII), which is reduced to 2-methoxy-1,4-dihydroxybenzene (IV). IV is oxidized by either LiP or MnP to generate 4-hydroxy-1,2-benzoquinone, which is reduced to 1,2,4-trihydroxybenzene (III). The other aromatic product generated by the initial LiP-catalyzed cleavage of I is 2-hydroxy-1,4-benzoquinone (VIII). This intermediate is also generated during the LiP- or MnP-catalyzed oxidation of the intermediate chlorocatechol (II). VIII is also reduced to 1,2,4-trihydroxybenzene (III). The key intermediate III is ring cleaved by intracellular cell extracts to produce, after reduction, beta-ketoadipic acid. In this pathway, initial oxidative cleavage of both C-O-C bonds in I by LiP generates two quinone products, 4-chloro-1,2-benzoquinone (V) and 2-hydroxy-1,4-benzoquinone (VIII). The former is recycled by reduction and methylation reactions to generate an intermediate which is also a substrate for peroxidase-catalyzed oxidation, leading to the removal of a second chlorine atom. This unique pathway results in the removal of both aromatic chlorines before aromatic ring cleavage takes place.     

Oxidative 4-dechlorination of 2,4,6-trichlorophenol catalyzed by horseradish peroxidase

 The well-known and easily available horseradish peroxidase (HRP) catalyzes the H₂O₂-dependent oxidative 4-dechlorination of the pollutant 2,4,6-trichlorophenol, which is recalcitrant to many organisms except those producing ligninases. UV-visible spectroscopy and gas chromatography-mass spectrometry identified the oxidized reaction product as 2,6-dichloro-1,4-benzoquinone. NMR and IR spectroscopic data further supported the above characterization. Experimental evidence for the elimination of HCl from the substrate was acquired by detecting the decrease in pH of the reaction mixture, and by observing the presence of the β-chlorocyclopentadienone cation fragment in the mass spectrum of 2,6-dichloro-1,4-benzoquinone. Consequently, nucleophilic attack by water on the 2,4,6-trichlorocyclohexadienone cation was proposed to give the final product. Our results indicate an oxidative dechlorination pathway catalyzed by HRP for 2,4,6-trichlorophenol, similar to that by extracellular lignin peroxidases. The relative catalytic efficiency of HRP seems higher than that of lignin peroxidases. The HRP-H₂O₂ catalytic system could be utilized in the degradation of polychlorinated phenols for industrial and biotechnological purposes. Received: 20 November 1998 / Accepted: 29 January 1999     

Specificity of reductive dehalogenation of substituted ortho-chlorophenols by Desulfitobacterium dehalogenans JW/IU-DC1.

Resting cells of Desulfitobacterium dehalogenans JW/IU-DC1 growth with pyruvate and 3-chloro-4-hydroxyphenylacetate (3-Cl-4-OHPA) as the electron acceptor and inducer of dehalogenation reductively ortho-dehalogenate pentachlorophenol (PCP); tetrachlorophenols (TeCPs); the trichlorophenols 2,3,4-TCP, 2,3,6-TCP, and 2,4,6-TCP; the dichlorophenols 2,3-DCP, 2,4-DCP, and 2,6-DCP; 2,6-dichloro-4-R-phenols (2,6-DCl-4-RPs, where R is -H, -F, -Cl, -NO2, -CO2, or -COOCH3; 2-chloro-4-R-phenols (2-Cl-4-RPs, where R is -H, -F, -Cl, -Br, -NO2, -CO2-, -CH2CO2, or -COOCH3); and the bromophenols 2-BrP, 2,6-DBrP, and 2-Br-4ClP [corrected]. Monochlorophenols, the dichlorophenols 2,5-DCP, 3,4-DCP, and 3,5-DCP, the trichlorophenols 2,3,5-TCP, 2,4,5-TCP, and 3,4,5-TCP, and the fluorinated analog of 3-Cl-4-OHPA, 3-F-4-OHPA ("2-F-4-CH2CO2- P"), are not dehalogenated. A chlorine substituent in position 3 (meta), 4 (para), or 6 (second ortho) of the phenolic moiety facilitates ortho dehalogenation in position 2. Chlorine in the 5 (second meta) position has a negative effect on the dehalogenation rate or even prevents dechlorination in the 2 position. In general, 2,6-DCl-4-RPs are dechlorinated faster than the corresponding 2-Cl-4-RPs with the same substituent R in the 4 position. The highest dechlorination rate, however, was found for dechlorination of 2,3-DCP, with a maximal observed first-order rate constant of 19.4 h-1 g (dry weight) of biomass-1.(ABSTRACT TRUNCATED AT 250 WORDS)     

Reductive dechlorination of chlorophenols by a pentachlorophenol- acclimated methanogenic consortium.

Anaerobic digester sludge fed 5,300 mg of acetate per liter, 3.4 microM pentachlorophenol, and nutrients for 10 days biotransformed pentachlorophenol by sequential ortho dechlorinations to produce 2,3,4,5-tetrachlorophenol and 3,4,5-trichlorophenol. Upon acclimation to 3.4 microM pentachlorophenol for 6 months, the methanogenic consortium removed chlorines from the ortho, meta, and para positions of pentachlorophenol and its reductive dechlorination products. Pentachlorophenol was degraded to produce 2,3,4,5-tetrachlorophenol, 2,3,4,6-tetrachlorophenol, and 2,3,5,6-tetrachlorophenol. Dechlorination of 2,3,4,5-tetrachlorophenol produced 3,4,5-trichlorophenol, which was subsequently degraded to produce 3,4-dichlorophenol and 3,5-dichlorophenol. 2,3,4,6-Tetrachlorophenol was dechlorinated at the ortho and meta positions to produce 2,4,6-trichlorophenol and 2,4,5-trichlorophenol. 2,3,5,6-Tetrachlorophenol yielded 2,3,5-trichlorophenol, followed by production of 3,5-dichlorophenol. 2,4,6-Trichlorophenol was degraded to form 2,4-dichlorophenol, and 2,4,5-trichlorophenol was dechlorinated at two positions to form 2,4-dichlorophenol and 3,4-dichlorophenol. Of the three dichlorophenols produced (2,4-dichlorophenol, 3,4-dichlorophenol, and 3,5-dichlorophenol), only 2,4-dichlorophenol was degraded significantly within 3 weeks, to produce 4-chlorophenol.     

Reductive dechlorination of chlorophenols by a pentachlorophenol- acclimated methanogenic consortium.

Anaerobic digester sludge fed 5,300 mg of acetate per liter, 3.4 microM pentachlorophenol, and nutrients for 10 days biotransformed pentachlorophenol by sequential ortho dechlorinations to produce 2,3,4,5-tetrachlorophenol and 3,4,5-trichlorophenol. Upon acclimation to 3.4 microM pentachlorophenol for 6 months, the methanogenic consortium removed chlorines from the ortho, meta, and para positions of pentachlorophenol and its reductive dechlorination products. Pentachlorophenol was degraded to produce 2,3,4,5-tetrachlorophenol, 2,3,4,6-tetrachlorophenol, and 2,3,5,6-tetrachlorophenol. Dechlorination of 2,3,4,5-tetrachlorophenol produced 3,4,5-trichlorophenol, which was subsequently degraded to produce 3,4-dichlorophenol and 3,5-dichlorophenol. 2,3,4,6-Tetrachlorophenol was dechlorinated at the ortho and meta positions to produce 2,4,6-trichlorophenol and 2,4,5-trichlorophenol. 2,3,5,6-Tetrachlorophenol yielded 2,3,5-trichlorophenol, followed by production of 3,5-dichlorophenol. 2,4,6-Trichlorophenol was degraded to form 2,4-dichlorophenol, and 2,4,5-trichlorophenol was dechlorinated at two positions to form 2,4-dichlorophenol and 3,4-dichlorophenol. Of the three dichlorophenols produced (2,4-dichlorophenol, 3,4-dichlorophenol, and 3,5-dichlorophenol), only 2,4-dichlorophenol was degraded significantly within 3 weeks, to produce 4-chlorophenol.     

Isolation and Characterization of Desulfovibrio dechloracetivorans sp. nov., a Marine Dechlorinating Bacterium Growing by Coupling the Oxidation of Acetate to the Reductive Dechlorination of 2-Chlorophenol

Strain SF3, a gram-negative, anaerobic, motile, short curved rod that grows by coupling the reductive dechlorination of 2-chlorophenol (2-CP) to the oxidation of acetate, was isolated from San Francisco Bay sediment. Strain SF3 grew at concentrations of NaCl ranging from 0.16 to 2.5%, but concentrations of KCl above 0.32% inhibited growth. The isolate used acetate, fumarate, lactate, propionate, pyruvate, alanine, and ethanol as electron donors for growth coupled to reductive dechlorination. Among the halogenated aromatic compounds tested, only the ortho position of chlorophenols was reductively dechlorinated, and additional chlorines at other positions blocked ortho dechlorination. Sulfate, sulfite, thiosulfate, and nitrate were also used as electron acceptors for growth. The optimal temperature for growth was 30°C, and no growth or dechlorination activity was observed at 37°C. Growth by reductive dechlorination was revealed by a growth yield of about 1 g of protein per mol of 2-CP dechlorinated, and about 2.7 g of protein per mole of 2,6-dichlorophenol dechlorinated. The physiological features and 16S ribosomal DNA sequence suggest that the organism is a novel species of the genus Desulfovibrio and which we have designated Desulfovibrio dechloracetivorans. The unusual physiological feature of this strain is that it uses acetate as an electron donor and carbon source for growth with 2-CP but not with sulfate.     

Reductive dechlorination of all trichloro- and dichlorobenzene isomers

Abstract All three isomers of trichlorobenzene were reductively dechlorinated to monochlorobenzene via dichlorobenzenes in anaerobic sediment columns. The dechlorination was specific: 1,2,3- and 1,3,5-trichlorobenzene were solely transformed to 1,3-dichlorobenzene, while 1,4-dichlorobenzene was the only product of 1,2,4-trichlorobenzene transformation. Microorganisms were responsible for the observed transformations. Since monochlorobenzene and dichlorobenzene are mineralized by bacteria in the presence of oxygen, the process of reductive dechlorination may be an important initial step to obtain complete mineralization of otherwise recalcitrant trichlorobenzenes. This is especially true for the 1,3,5-isomer, which seems to resist biodegradation in oxic environments.     

Degradation of 2,4-dichlorophenol by the lignin-degrading fungus Phanerochaete chrysosporium.

Under secondary metabolic conditions the white rot basidiomycete Phanerochaete chrysosporium mineralizes 2,4-dichlorophenol (I). The pathway for the degradation of 2,4-dichlorophenol (I) was elucidated by the characterization of fungal metabolites and of oxidation products generated by purified lignin peroxidase and manganese peroxidase. The multistep pathway involves the oxidative dechlorination of 2,4-dichlorophenol (I) to yield 1,2,4,5-tetrahydroxybenzene (VIII). The intermediate 1,2,4,5-tetrahydroxybenzene (VIII) is ring cleaved to produce, after subsequent oxidation, malonic acid. In the first step of the pathway, 2,4-dichlorophenol (I) is oxidized to 2-chloro-1,4-benzoquinone (II) by either manganese peroxidase or lignin peroxidase. 2-Chloro-1,4-benzoquinone (II) is then reduced to 2-chloro-1,4-hydroquinone (III), and the latter is methylated to form the lignin peroxidase substrate 2-chloro-1,4-dimethoxybenzene (IV). 2-Chloro-1,4-dimethoxybenzene (IV) is oxidized by lignin peroxidase to generate 2,5-dimethoxy-1,4-benzoquinone (V), which is reduced to 2,5-dimethoxy-1,4-hydroquinone (VI). 2,5-Dimethoxy-1,4-hydroquinone (VI) is oxidized by either peroxidase to generate 2,5-dihydroxy-1,4-benzoquinone (VII) which is reduced to form the tetrahydroxy intermediate 1,2,4,5-tetrahydroxybenzene (VIII). In this pathway, the substrate is oxidatively dechlorinated by lignin peroxidase or manganese peroxidase in a reaction which produces a p-quinone. The p-quinone intermediate is then recycled by reduction and methylation reactions to regenerate an intermediate which is again a substrate for peroxidase-catalyzed oxidative dechlorination. This unique pathway apparently results in the removal of both chlorine atoms before ring cleavage occurs.     

Dehalorespiration with hexachlorobenzene and pentachlorobenzene by<Emphasis Type="Italic"> Dehalococcoides</Emphasis> sp. strain CBDB1

The chlororespiring anaerobe Dehalococcoides sp. strain CBDB1 used hexachlorobenzene and pentachlorobenzene as electron acceptors in an energy-conserving process with hydrogen as electron donor. Previous attempts to grow Dehalococcoides sp. strain CBDB1 with hexachlorobenzene or pentachlorobenzene as electron acceptors failed if these compounds were provided as solutions in hexadecane. However, Dehalococcoides sp. strain CBDB1 was able to grow with hexachlorobenzene or pentachlorobenzene when added in crystalline form directly to cultures. Growth of Dehalococcoides sp. strain CBDB1 by dehalorespiration resulted in a growth yield (Y) of 2.1±0.24 g protein/mol Cl^– released with hexachlorobenzene as electron acceptor; with pentachlorobenzene, the growth yield was 2.9±0.15 g/mol Cl^–. Hexachlorobenzene was reductively dechlorinated to pentachlorobenzene, which was converted to a mixture of 1,2,3,5- and 1,2,4,5-tetrachlorobenzene. Formation of 1,2,3,4-tetrachlorobenzene was not detected. The final end-products of hexachlorobenzene and pentachlorobenzene dechlorination were 1,3,5-trichlorobenzene, 1,3- and 1,4-dichlorobenzene, which were formed in a ratio of about 3:2:5. As reported previously, Dehalococcoides sp. strain CBDB1 converted 1,2,3,5-tetrachlorobenzene exclusively to 1,3,5-trichlorobenzene, and 1,2,4,5-tetrachlorobenzene exclusively to 1,2,4-trichlorobenzene. The organism therefore catalyzes two different pathways to dechlorinate highly chlorinated benzenes. In the route leading to 1,3,5-trichlorobenzene, only doubly flanked chlorine substituents were removed, while in the route leading to 1,3-and 1,4-dichlorobenzene via 1,2,4-trichlorobenzene singly flanked chlorine substituents were also removed. Reductive dehalogenase activity measurements using whole cells pregrown with different chlorobenzene congeners as electron acceptors indicated that different reductive dehalogenases might be induced by the different electron acceptors. To our knowledge, this is the first report describing reductive dechlorination of hexachlorobenzene and pentachlorobenzene via dehalorespiration by a pure bacterial culture.     

Isolation and characterization of Desulfovibrio dechloracetivorans sp. nov., a marine dechlorinating bacterium growing by coupling the oxidation of acetate to the reductive dechlorination of 2-chlorophenol

Strain SF3, a gram-negative, anaerobic, motile, short curved rod that grows by coupling the reductive dechlorination of 2-chlorophenol (2-CP) to the oxidation of acetate, was isolated from San Francisco Bay sediment. Strain SF3 grew at concentrations of NaCl ranging from 0.16 to 2.5%, but concentrations of KCl above 0. 32% inhibited growth. The isolate used acetate, fumarate, lactate, propionate, pyruvate, alanine, and ethanol as electron donors for growth coupled to reductive dechlorination. Among the halogenated aromatic compounds tested, only the ortho position of chlorophenols was reductively dechlorinated, and additional chlorines at other positions blocked ortho dechlorination. Sulfate, sulfite, thiosulfate, and nitrate were also used as electron acceptors for growth. The optimal temperature for growth was 30 degrees C, and no growth or dechlorination activity was observed at 37 degrees C. Growth by reductive dechlorination was revealed by a growth yield of about 1 g of protein per mol of 2-CP dechlorinated, and about 2.7 g of protein per mole of 2,6-dichlorophenol dechlorinated. The physiological features and 16S ribosomal DNA sequence suggest that the organism is a novel species of the genus Desulfovibrio and which we have designated Desulfovibrio dechloracetivorans. The unusual physiological feature of this strain is that it uses acetate as an electron donor and carbon source for growth with 2-CP but not with sulfate.     

Reductive dehalogenation of chlorinated benzenes and toluenes under methanogenic conditions.

The anaerobic metabolism of chlorinated benzenes and toluenes was evaluated in soil slurry microcosms under methanogenic conditions. A mixture of hexachlorobenzene, pentachlorobenzene, and 1,2,4-trichlorobenzene (TCB) in soil slurries was biotransformed through sequential reductive dechlorination to chlorobenzene (CB). The metabolic pathway for hexachlorobenzene and pentachlorobenzene decay proceeded via 1,2,3,4-tetrachlorobenzene (TTCB)-->1,2,3-TCB + 1,2,4-TCB-->1,2-dichlorobenzene (DCB) + 1,4-DCB-->CB. In a mineral salts medium, the CB-adapted soil microorganisms dehalogenated individual 1,2,4,5-TTCB, 1,2,3,4-TTCB, 1,2,3-TCB, and 1,2,4-TCB but not 1,2,3,5-TTCB or 1,3,5-TCB. Similarly, a mixture of 2,3,6-trichlorotoluene (TCT), 2,5-dichlorotoluene (DCT), and 3,4-DCT was reductively dechlorinated in soil slurries to predominantly toluene and small amounts of 2-, 3-, and 4-chlorotoluene (CT). Toluene was further degraded. When tested individually in a mineral salts medium, the CT-adapted soil microorganisms dechlorinated several TCT and DCT isomers. Key metabolic routes for TCTs followed: 2,3,6-TCT-->2,5-DCT-->2-CT-->toluene; 2,4,5-TCT-->2,5-DCT + 3,4-DCT-->3-CT + 4-CT-->toluene. Among DCTs tested, 2,4-DCT and 3,4-DCT were dechlorinated via the removal of o- and m-chlorine, respectively, to 4-CT and subsequently to toluene via p-chlorine removal. Likewise, 2,5-DCT was dechlorinated via 2-CT to toluene. Evidently, microorganisms capable of removing o-, m-, and p-chlorines are present in the soil system, as reflected by the dechlorination of different isomers of CBs and CTs to CB and toluene, respectively. These findings help clarify the metabolic fate of chlorinated benzenes and toluenes in anaerobic environments.     

Purification and Characterization of Hydroxyquinol 1,2-Dioxygenase from Azotobacter sp. Strain GP1

Hydroxyquinol 1,2-dioxygenase was purified from cells of the soil bacterium Azotobacter sp. strain GP1 grown with 2,4,6-trichlorophenol as the sole source of carbon. The presumable function of this dioxygenase enzyme in the degradative pathway of 2,4,6-trichlorophenol is discussed. The enzyme was highly specific for 6-chlorohydroxyquinol (6-chloro-1,2,4-trihydroxybenzene) and hydroxyquinol (1,2,4-trihydroxybenzene) and was found to perform ortho cleavage of the hydroxyquinol compounds, yielding chloromaleylacetate and maleylacetate, respectively. With the conversion of 1 mol of 6-chlorohydroxyquinol, the consumption of 1 mol of O(inf2) and the formation of 1 mol of chloromaleylacetate were observed. Catechol was not accepted as a substrate. The enzyme has to be induced, and no activity was found in cells grown on succinate. The molecular weight of native hydroxyquinol 1,2-dioxygenase was estimated to 58,000, with a sedimentation coefficient of 4.32. The subunit molecular weight of 34,250 indicates a dimeric structure of the dioxygenase enzyme. The addition of Fe(sup2+) ions significantly activated enzyme activity, and metal-chelating agents inhibited it. Electron paramagnetic resonance data are consistent with high-spin iron(III) in a rhombic environment. The NH(inf2)-terminal amino acid sequence was determined for up to 40 amino acid residues and compared with sequences from literature data for other catechol and chlorocatechol dioxygenases.     

Transformation of 2,4,6-trichlorophenol by free and immobilized fungal laccase

Laccase from the white rot fungus Coriolus versicolor was immobilized on Celite R-637 by covalent binding with glutaraldehyde. After a sharp primary decline in activity (up to 50%), the retained enzyme activity was stable over a storage period of 33 days at 4 degrees C. A comparative study of soluble and immobilized laccases revealed the increased resistance of immobilized enzyme to the unfavourable effects of alkaline pH, high temperature and the action of inhibitors. A combination of these properties of immobilized laccase resulted in the ability to oxidize 2,4,6-trichlorophenol (2,4,6-TCP) at 50 degrees C at pH 7.0. The reactions of soluble and immobilized laccase with 2,4,6-TCP were examined in the presence and absence of redox mediators. 3,5-Dichlorocatechol, 2,6-dichloro-1,4-benzoquinone and 2,6-dichloro-1,4-hydroquinone were found to be the primary products of 2,4,6-TCP oxidation by laccase; oligo- and polymeric compounds were also found.     

Dechlorination of polychlorinated biphenyl congeners by an anaerobic microbial consortium

  An anaerobic methanogenic microbial consortium, developed in a granular form, exhibited extensive dechlorination of defined polychlorinated biphenyl (PCB) congeners. A 2,3,4,5,6-pentachlorobiphenyl was dechlorinated to biphenyl via 2,3,4,6-tetrachlorobiphenyl, 2,4,6-trichlorobiphenyl, 2,4-dichlorobi-phenyl and 2-chlorobiphenyl (CB). Removal of chlorine atoms from all three positions of the biphenyl ring, i.e., ortho, meta and para, was observed during this reductive dechlorination process. Biphenyl was identified as one of the end-products of the reductive dechlorination by GC-MS. After 20 weeks, the concentrations of the dechlorination products 2,4,6-CB, 2,4-CB, 2-CB and biphenyl were 8.1, 41.2, 3.0 and 47.8 μM respectively, from an initial 105 μM 2,3,4,5,6-CB. The extent and pattern of the dechlorination were further confirmed by the dechlorination of lightly chlorinated congeners including 2-CB, 3-CB, 4-CB, 2,4-CB and 2,6-CB individually. This study indicates that the dechlorination of 2,3,4,5,6-CB to biphenyl is due to ortho, meta and para dechlorination by this anaerobic microbial consortium. Received: 30 April 1996 / Received revision: 26 July 1996 / Accepted: 5 August 1996     

Enhanced dechlorination of 2,4,6-trichlorophenol by anaerobic microbial populations in the presence of ethanol

Summary A consortium of anaerobic microorganisms was grown on acetate, ethanol, glucose or methanol and dechlorinated 50 umol 2,4,6-trichlorophenol, through 2,4-dichlorophenol, to 4-chlorophenol. The highest rate of dechlorination of 2,4,6-trichlorophenol was observed when ethanol was used as a growth substrate.     

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.     

Catabolism of 4-hydroxybenzoate in Candida parapsilosis proceeds through initial oxidative decarboxylation by a FAD-dependent 4-hydroxybenzoate 1-hydroxylase

Abstract The first two steps in the catabolism of 4-hydroxybenzoate by the ascomycetous yeast Candida parapsilosis CBS604 were investigated. In contrast to the well-known bacterial pathways and to what was previously assumed, metabolism of 4-hydroxybenzoate in C. parapsilosis proceeds through initial oxidative decarboxylation to give 1,4-dihydroxybenzene. This reaction is catalyzed by a NAD(P)H and FAD-dependent 4-hydroxybenzoate 1-hydroxylase. Further metabolism of 1,4-dihydroxybenzene to the ring-fission substrate 1,2,4-trihydroxybenzene is catalyzed by a NADPH-specific FAD-dependent aromatic hydroxylase acting on phenolic compounds. ¹⁹F-NMR experiments with cell extracts and 2-fluoro-4-hydroxybenzoate as the model compound confirm this metabolic pathway and exclude the alternative pathway proceeding through initial 3-hydroxylation followed by oxidative decarboxylation in the second step.     

Degradation of diphenyl ether herbicides by the lignin-degrading basidiomycete Coriolus versicolor

Under ligninolytic conditions, the white-rot basidiomycete Coriolus versicolor metabolized chloronitrofen (2, 4, 6-trichloro-4'-nitrodiphenyl ether; CNP) and nitrofen (2, 4-dichloro-4'-nitrodiphenyl ether, NIP), which constitute the largest class of commercially produced diphenyl ether herbicides. The pathway of CNP degradation was elucidated by the identification of fungal metabolites upon addition of CNP and its metabolic intermediates. The metabolic pathway was initially branched to form four metabolites--2, 4, 6-trichloro-3-hydroxy-4'-nitrodiphenyl ether, 2, 4-dichloro-6-hydroxy-4'-nitrodiphenyl ether, NIP, and 2, 4, 6-trichloro-4'-aminodiphenyl ether--indicating the involvement of hydroxylation, oxidative dechlorination, reductive dechlorination, and nitro-reduction. Of these reactions, hydroxylation was relatively major compared to the others. Extracellular ligninolytic enzymes such as lignin peroxidase, manganese peroxidase and laccase did not catalyze the oxidation of either CNP or NIP. Piperonyl butoxide, an inhibitor of cytochrome P450, suppressed fungal oxidation of CNP and NIP to their hydroxylated products. The inhibition resulted in increasing the amount of reductively dechlorinated and nitro-reduced products. These observations strongly suggest that basidiomycetes may possess a mechanism for a strict substrate recognition system and a corresponding metabolic response system to effectively degrade environmentally persistent aromatic compounds.