Influence of chlorobenzoates on the utilisation of chlorobiphenyls and chlorobenzoate mixtures by chlorobiphenyl/chlorobenzoate-mineralising hybrid bacterial strains

Chlorobenzoates (CBA) arise as intermediates during the degradation of polychlorinated biphenyls (PCBs) and some chlorinated herbicides. Since PCBs were produced as complex mixtures, a range of mono-, di-, and possibly trichloro-substituted benzoates would be formed. Chlorobenzoate degradation has been proposed to be one of the rate-limiting steps in the overall PCB-degradation process. Three hybrid bacteria constructed to have the ability to completely mineralise 2-, 3-, or 4-monochlorobiphenyl respectively, have been studied to establish the range of mono- and diCBAs that can be utilised. The three strains were able to mineralise one or more of the following CBAs: 2-, 3-, and 4-monochlorobenzoate and 3,5-dichlorobenzoate. No utilisation of 2,3-, 2,5-, 2,6-, or 3,4-diCBA was observed, and only a low concentration (0.11 mM) of 2,4-diCBA was mineralised. When the strain with the widest substrate range (Burkholderia cepacia JHR22) was simultaneously supplied with two CBAs, one that it could utilise plus one that it was unable to utilise, inhibitory effects were observed. The utilisation of 2-CBA (2.5 mM) by this strain was inhibited by 2,3-CBA (200 M) and 3,4-CBA (50 M). Although 2,5-CBA and 2,6-CBA were not utilised as carbon sources by strain JHR22, they did not inhibit 2-CBA utilisation at the concentrations studied, whereas 2,4-CBA was co-metabolised with 2-CBA. The utilisation of 2-, 3-, and 4-chlorobiphenyl by strain JHR22 was also inhibited by the presence of 2,3- or 3,4-diCBA. We conclude that the effect of the formation of toxic intermediates is an important consideration when designing remediation strategies.Abbreviations PCB Polychlorinated biphenyl - CBA Chlorobenzoate     

Influence of chlorobenzoic acids on the growth and degradation potentials of PCB-degrading microorganisms

The biodegradation of polychlorinated biphenyls (PCBs) by diverse bacteria including those utilized in this study is often incomplete, a concomitant accumulation of chlorobenzoic acids (CBAs) are released as dead-end products. The build-up of these metabolites in the growth medium may result in feed-back inhibition and impede PCB biotransformation. In this investigation using GC-ECD and HPLC analyses, we confirmed that CBAs inhibit growth and PCB biodegradation potentials of five tropical bacteria namely, Pseudomonas aeruginosa SA-1, Enterobacter sp. SA-2, Ralstonia sp. SA-3, Ralstonia sp. SA-5 and Pseudomonas sp. SA-6. Among the four CBAs (2-CBA, 3-CBA, 4-CBA acids and 2,3-diCBA), 3-CBA was the strongest inhibitor followed by 4-CBA. Furthermore, we found that 3-CBA heavily inhibited growth of SA-3 and SA-6 on monochlorobiphenyls by 82–90% while elimination rate was inhibited by 71–88%. In the case of 2,3-diCBA, inhibition was generally less than 60%. However, effects of both acids were stronger in SA-3 than SA-6. We also found that 3-CBA and 2,3-diCBA completely inhibited carbon-chloride cleavage of 2-CB and 3-CB since cultivation in the absence of the acids resulted in recovery of 23–50% chloride in the culture fluids of organisms. These findings may therefore, have practical and ecological significance and are useful for improving the efficiency and the stability of some biological treatment processes.     

Biological degradation of 4-chlorobenzoic acid by a PCB-metabolizing bacterium through a pathway not involving (chloro)catechol

Cupriavidus sp. strain SK-3, previously isolated on polychlorinated biphenyl mixtures, was found to aerobically utilize a wide spectrum of substituted aromatic compounds including 4-fluoro-, 4-chloro- and 4-bromobenzoic acids as a sole carbon and energy source. Other chlorobenzoic acid (CBA) congeners such as 2-, 3-, 2,3-, 2,5-, 3,4- and 3,5-CBA were all rapidly transformed to respective chlorocatechols (CCs). Under aerobic conditions, strain SK-3 grew readily on 4-CBA to a maximum concentration of 5 mM above which growth became impaired and yielded no biomass. Growth lagged significantly at concentrations above 3 mM, however chloride elimination was stoichiometric and generally mirrored growth and substrate consumption in all incubations. Experiments with resting cells, cell-free extracts and analysis of metabolite pools suggest that 4-CBA was metabolized in a reaction exclusively involving an initial hydrolytic dehalogenation yielding 4-hydroxybenzoic acid, which was then hydroxylated to protocatechuic acid (PCA) and subsequently metabolized via the β-ketoadipate pathway. When strain SK-3 was grown on 4-CBA, there was gratuitous induction of the catechol-1,2-dioxygenase and gentisate-1,2-dioxygenase pathways, even if both were not involved in the metabolism of the acid. While activities of the modified ortho- and meta-cleavage pathways were not detectable in all extracts, activity of PCA-3,4-dioxygenase was over ten-times higher than those of catechol-1,2- and gentisate-1,2-dioxygenases. Therefore, the only reason other congeners were not utilized for growth was the accumulation of CCs, suggesting a narrow spectrum of the activity of enzymes downstream of benzoate-1,2-dioxygenase, which exhibited affinity for a number of substituted analogs, and that the metabolic bottlenecks are either CCs or catabolites of the modified ortho-cleavage metabolic route.     

Degradation of mono- and dichlorobenzoic acid isomers by two natural isolates of Alcaligenes denitrificans

Two strains of Alcaligenes denitrificans, designated BRI 3010 and BRI 6011, were isolated from polychlorinated biphenyl (PCB)-contaminated soil using 2,5-dichlorobenzoic acid (2,5-DCBA) and 2,4-DCBA, respectively, as sole carbon and energy sources. Both strains degraded 2-chlorobenzoic acid (2-CBA), 2,3-DCBA, and 2,5-DCBA, and were unable to degrade 2,6-DCBA. BRI 6011 alone degraded 2,4-DCBA. Growth of BRI 6011 in yeast extract and 2,6-DCBA induced pyrocatechase activity, but 2,6-DCBA was not degraded, suggesting the importance of an unsubstituted carbon six of the aromatic ring. Metabolism of the chlorinated substrates resulted in the stoichiometric release of chloride, and degradation proceeded by intradiol cleavage of the aromatic ring. Growth of both strains on 2,5-DCBA induced pyrocatechase activities with catechol and chlorocatechols as substrates. In contrast to dichlorobenzoic acids, growth on 2-CBA, benzoic acid, mono- and dihydroxybenzoic acids induced a pyrocatechase activity against catechol only. Although 2,4-DCBA was a more potent inducer of both pyrocatechase activities, its utilization by BRI 6011 was inhibited by 2,5-DCBA. Specific uptake rates using resting cells were highest with 2-CBA, except when the resting cells had been previously grown on 2,5-DCBA, in which case 2,5-DCBA was the preferred substrate. The higher rates of 2,5-DCBA uptake obtained by growth on that substrate, suggested the existence of a separately induced uptake system for 2,5-DCBA.     

Isolation and characterization of a 2,4-dichlorophenoxyacetic acid-degrading soil bacterium

Summary A 2,4-dichlorophenoxyacetic acid (2,4-D)-degrading bacterial strain, Xanthobacter sp. CP, was isolated after enrichment in aerated soil columns. A limited number of chlorinated phenols and chlorinated phenoxyalkanoic acids with an even number of carbon atoms in the side chain served as substrates for growth, although whole cells exhibited oxygen uptake with a wide range of those compounds. The maximal growth rate with 2,4-D was 0.13·h^-1 at a growth yield of 0.1 g biomass/g 2,4-D. Chloride ions were released quantitatively from 2,4-D and related chlorinated aromatic compounds which served as growth substrates. No by-products of 2,4-D metabolism were detected in oxygen-sufficient cultures of Xanthobacter sp. CP and catechols were cleaved exclusively by catechol 1,2-dioxygenase.     

Pathways for 3-chloro- and 4-chlorobenzoate degradationin Pseudomonas aeruginosa 3mT

A bacterial isolate, Pseudomonas aeruginosa 3mT, exhibited the ability to degrade high concentrations of 3-chlorobenzoate (3-CBA, 8 g l^-1) and 4-chlorobenzoate (4-CBA 12 g l^-1) (Ajithkumar 1998). In this study, by delineating the initial biochemical steps involved in the degradation of these compounds, we investigated how this strain can do so well. Resting cells, permeabilised cells as well as cell-free extracts failed to dechlorinate both 3-CBA and 4-CBA under anaerobic conditions, whereas the former two readily degraded both compounds under aerobic conditions. Accumulation of any intermediary metabolite was not observed during growth as well as reaction with resting cells under highly aerated conditions. However, on modification of reaction conditions, 3-chlorocatechol (3-CC) and 4-chlorocatechol (4-CC) accumulated in 3-CBA and 4-CBA flasks, respectively. Fairly high titres of pyrocatechase II (chlorocatechol 1,2-dioxygenase) activity were obtained in extracts of cells grown on 3-CBA and 4-CBA. Meta-pyrocatechase (catechol 2,3-dioxygenase) activity against4-CC and catechol, but not against 3-CC, was also detected in low titres. Accumulation of small amounts of 2-chloro-5-hydroxy muconic semialdehyde, the meta-cleavage product of 4-CC, was detected in the medium, when 4-CBA concentration was 4 mM or greater, indicating the presence of a minor meta-pathway in strain 3mT. However, 3-CBA exclusively, and more than 99% of 4-CBA were degraded through the formation of the respective chlorocatechol, via a modified ortho-pathway. This defies the traditional view that the microbes that follow chlorocatechol pathways are not very good degraders of chlorobenzoates. 4-Hydroxybenzoatewas readily (and 3-hydroxybenzoate to a lesser extent) degraded by the strain, through the formation of protocatechuate and gentisate, respectively, as intermediary dihydroxy metabolites.     

In vitro degradation of fluoranthene by bacteria isolated from petroleum sludge

An investigation was carried out for in vitro degradation of fluoranthene by four bacterial strains (PSM6, PSM7, PSM10 and PSM11) isolated from the petroleum sludge. Although all the strains registered their growth in MSM with 100 ppm fluoranthene, PSM11 growth was better than other strains. Growth of bacterial strains invariably corresponded to their degradation potential of fluoranthene. After 168 h of incubation, 61% fluoranthene was degraded by PSM11, followed by PSM10 (48%) and PSM6 (42%) and the least was recorded in PSM7 (41%). Besides, 11% loss in fluoranthene was attributed to abiotic factors. Thirty-eight times more activity of catechol 2,3-dioxygenase than catechol 1,2-dioxygenase showed that it played a significant role in fluoranthene degradation. Molecular weight of catechol 2,3-dioxygenase isolated from PSM11 was determined as ∼136 kDa by size exclusion chromatography and 34 kDa on denaturing SDS-PAGE, indicating tetrameric nature of the enzyme.     

The Effects of Cyanobacterial Exudates on Bacterial Growth and Biodegradation of Organic Contaminants

The pulp and paper industry largely depends on the biodegradation activities of heterotrophic bacteria to remove organic contaminants in wastewater prior to discharge. Our recent discovery of extensive cyanobacterial communities in pulp and paper waste treatment systems led us to investigate the potential impacts of cyanobacterial exudates on growth and biodegradation efficiency of three bacterial heterotrophs. Each of the three assessed bacteria represented different taxa commonly found in pulp and paper waste treatment systems: a fluorescent Pseudomonad, an Ancylobacter aquaticus strain, and a Ralstonia eutropha strain. They were capable of utilizing phenol, dichloroacetate (DCA), or 2,4-dichlorophenoxyacetic acid (2,4-D), respectively. Exudates from all 12 cyanobacterial strains studied supported the growth of each bacterial strain to varying degrees. Maximum biomass of two bacterial strains positively correlated with the total organic carbon content of exudate treatments. The combined availability of exudate and a known growth substrate (i.e., phenol, DCA, or 2,4-D) generally had a synergistic affect on the growth of the Ancylobacter strain, whereas mixed effects were seen on the other two strains. Exudates from four representative cyanobacterial strains were assessed for their impacts on phenol and DCA biodegradation by the Pseudomonas and Ancylobacter strains, respectively. Exudates from three of the four cyanobacterial taxa repressed phenol biodegradation, but enhanced DCA biodegradation. These dissimilar impacts of cyanobacterial exudates on bacterial degradation of contaminants suggest a species-specific association, as well as a significant role for cyanobacteria during the biological treatment of wastewaters.     

Cloning, expression, and nucleotide sequence of the Pseudomonas aeruginosa 142 ohb genes coding for oxygenolytic ortho dehalogenation of halobenzoates

We have cloned and characterized novel oxygenolytic ortho-dehalogenation (ohb) genes from 2-chlorobenzoate (2-CBA)- and 2,4-dichlorobenzoate (2,4-dCBA)-degrading Pseudomonas aeruginosa 142. Among 3,700 Escherichia coli recombinants, two clones, DH5alphaF'(pOD22) and DH5alphaF'(pOD33), converted 2-CBA to catechol and 2,4-dCBA and 2,5-dCBA to 4-chlorocatechol. A subclone of pOD33, plasmid pE43, containing the 3,687-bp minimized ohb DNA region conferred to P. putida PB2440 the ability to grow on 2-CBA as a sole carbon source. Strain PB2440(pE43) also oxidized but did not grow on 2,4-dCBA, 2,5-dCBA, or 2,6-dCBA. Terminal oxidoreductase ISPOHB structural genes ohbA and ohbB, which encode polypeptides with molecular masses of 20,253 Da (beta-ISP) and 48,243 Da (alpha-ISP), respectively, were identified; these proteins are in accord with the 22- and 48-kDa (as determined by sodium dodecyl sulfate-polyacrylamide gel electrophoresis) polypeptides synthesized in E. coli and P. aeruginosa parental strain 142. The ortho-halobenzoate 1,2-dioxygenase activity was manifested in the absence of ferredoxin and reductase genes, suggesting that the ISPOHB utilized electron transfer components provided by the heterologous hosts. ISPOHB formed a new phylogenetic cluster that includes aromatic oxygenases featuring atypical structural-functional organization and is distant from the other members of the family of primary aromatic oxygenases. A putative IclR-type regulatory gene (ohbR) was located upstream of the ohbAB genes. An open reading frame (ohbC) of unknown function that overlaps lengthwise with ohbB but is transcribed in the opposite direction was found. The ohbC gene codes for a 48,969-Da polypeptide, in accord with the 49-kDa protein detected in E. coli. The ohb genes are flanked by an IS1396-like sequence containing a putative gene for a 39,715-Da transposase A (tnpA) at positions 4731 to 5747 and a putative gene for a 45,247-Da DNA topoisomerase I/III (top) at positions 346 to 1563. The ohb DNA region is bordered by 14-bp imperfect inverted repeats at positions 56 to 69 and 5984 to 5997.     

Cometabolic degradation of mono-chloro benzoic acids by <Emphasis Type="Italic">Rhodococcus</Emphasis> sp. R04 grown on organic carbon sources

The aerobic cometabolism of chlorobenzoic acids (CBAs) by Rhodococcus sp. R04 was accomplished by augmenting the medium with organic carbon sources. In mineral medium supplemented with glucose (MMG), 0.5 mM 2-CBA was incompletely metabolized after the 5-day incubation, while the near-complete disappearance of 0.5 mM 4-CBA was monitored. Over the 5-day incubation period, the concentration of chloride increased to 0.17 mM in bottles containing 4-CBA, glucose and strain R04; whereas in cultivation with 2-CBA the chloride content was about 0.1 mM. After 5-day incubation, 28.5% 4-CBA was remained in mineral medium supplemented with ethanol (MME), and the relatively low values of chloride were released. To our knowledge, it is first report that the feasibility of using ethanol as an added substrate for cometabolic degradation of CBA by aerobic polychlorinated biphenyl (PCB)-degrading bacteria. The specific activities of (chloro)benzoate 1,2-dioxygenase and (chloro)catechol 1,2-dioxygenase activities were detected in cell-free extracts (CFEs) of strain R04. These results suggest that the initial degradation of CBAs occurred most likely prior to chloride release.     

Effect of inoculant strain and organic matter content on kinetics of 2,4-dichlorophenoxyacetic acid degradation in soil.

We monitored rates of degradation of soluble and sorbed 2,4-dichlorophenoxyacetic acid (2,4-D) in low-organic-matter soil at field capacity amended with 1, 10, or 100 micrograms of 2,4-D per g of wet soil and inoculated with one of two bacterial strains (MI and 155) with similar maximum growth rates (mu max) but significantly different half-saturation growth constants (Ks). Concentrations of soluble 2,4-D were determined by analyzing samples of pore water pressed from soil, and concentrations of sorbed 2,4-D were determined by solvent extraction. Between 65 and 75% of the total 2,4-D was present in the soluble phase at equilibrium, resulting in soil solution concentrations of ca. 8, 60, and 600 micrograms of 2,4-D per ml, respectively. Soluble 2,4-D was metabolized preferentially; this was followed by degradation of both sorbed (after desorption) and soluble 2,4-D. Rates of degradation were comparable for the two strains at soil concentrations of 10 and 100 micrograms of 2,4-D per g; however, at 1 microgram/g of soil, 2,4-D was metabolized more rapidly by the strain with the lower Ks value (strain MI). We also monitored rates of biodegradation of soluble and sorbed 2,4-D in high-organic-matter soil at field capacity amended with 100 micrograms of 2,4-D per g of wet soil and inoculated with the low-Ks strain (strain MI). Ten percent of total 2,4-D was present in the soluble phase, resulting in a soil solution concentration of ca. 30 micrograms of 2,4-D per ml.(ABSTRACT TRUNCATED AT 250 WORDS)     

Hydrolytic dehalogenation of 4-chlorobenzoic acid by an Acinetobacter sp

Acinetobacter sp. strain ST-1, isolated from garden soil, can mineralize 4-chlorobenzoic acid (4-CBA). The bacterium degrades 4-CBA, starting with dehalogenation to yield 4-hydroxybenzoic acid (4-HBA) under both aerobic and anaerobic conditions, suggesting that the dehalogenating enzyme in the strain is not an oxygenase; the enzyme may catalyze halide hydrolysis. To identify the oxygen source of the C(4)-hydroxy groups in the dehalogenation step, we used H(2)(18)O as the solvent under anaerobic conditions. When resting cells were incubated in the presence of 4-CBA and H(2)(18)O under a nitrogen gas stream, the hydroxy group on the aromatic nucleus of the 4-HBA produced was derived from water, not from molecular oxygen. This dehalogenation was hydrolytic, because analysis of the mass spectrum of the trimethylsilyl derivative of one of the metabolites, (18)O-labeled 4-HBA, showed that 80% of the C4-hydroxy groups were labeled with (18)O. Hydrolytic dehalogenation of 4-CBA in intact cells has not been reported earlier. To identify substrate specificity, we next examined the ability of the strain to dehalogenate 4-CBA analogues and dichlorobenzoic acids. The results of metabolite analysis by high-pressure liquid chromatography showed that the strain dehalogenated 4-bromobenzoic acid and 4-iodobenzoic acid, yielding 4-HBA, suggesting that these compounds could be further degraded and mineralized by the strain via the beta-ketoadipate pathway, as occurs with 4-CBA. This strain, however, did not dehalogenate 4-fluorobenzoic acid, 2- and 3-chlorobenzoic acids, or 2,4-, 3,4-, and 3,5-dichlorobenzoic acids during 4 days of incubation, implying that the dehalogenating enzyme of the strain has high substrate specificity.     

Observations on the bacterial oxidation of chlorophenoxyacetic acids

Summary Three bacterial strains, one ofF. peregrinum (Stapp and Spicher) and two Achromobacter strains, have been isolated from soil and shown to decompose either 2,4-D, MCPA orp-chlorophenoxyacetic acid. Aerobic conditions are essential for the bacterial decomposition of 2,4-D. Pretreatment of soil with one of the three chlorophenoxyacetic acids accelerated the rate of breakdown of either of the other two. In a liquid medium, growth of theF. peregrinum strain caused breakdown of 2,4-D and liberated 76% of the chlorine in 2,4-D in ionic form. An unknown acidic substance, colourless in acid solution but forming a yellow sodium salt has been detected in cultures ofF. peregrinum or an MCPA-decomposing Achromobacter strain growing inp-chlorophenoxyacetate medium. The bacterial oxidation of chlorophenoxyacetic acid herbicides was attributed to adaptive enzyme formation. Respiration experiments showed that the oxidation of 2,4-D or ofp-chlorophenoxyacetic acid is incomplete. 4-Chloro-2-hydroxyphenoxyacetic acid and 4-chlorocatechol may be metabolic intermediates in the case ofp-chlorophenoxyacetic acid, but no intermediary metabolites have as yet been established for 2,4-D.     

Flavonol 2,4-dioxygenase from Aspergillus niger DSM 821, a type 2 CuII-containing glycoprotein.

Flavonol 2,4-dioxygenase, which catalyzes the cleavage of quercetin to carbon monoxide and 2-protocatechuoyl-phloroglucinol carboxylic acid, was purified from culture filtrate of Aspergillus niger DSM 821 grown on rutin. It is a glycoprotein (46-54% carbohydrate) with N-linked oligo-mannose type glycan chains. The enzyme was resolved in SDS polyacrylamide gels in a diffuse protein band that corresponded to a molecular mass of 130-170 kDa. When purified flavonol 2,4-dioxygenase was heated, it dissociated into three peptides with apparent molecular masses of 63-67 kDa (L), 53-57 kDa (M), and 31-35 kDa (S), which occurred in a molar ratio of 1:1:1, suggesting a LMS structure. Crosslinking led to a 90-97 kDa species, concomitant with the decrease of staining intensity of the 63-67 kDa (L) and the 31-35 kDa (S) peptides. Analysis by matrix-assisted laser desorption/ionization-time of flight-MS showed peaks at m/z approximately 69 600, m/z approximately 51 700, and m/z approximately 26 500 which are presumed to represent the three peptides of flavonol 2,4-dioxygenase, and a broad peak at m/z approximately 96 300, which might correspond to the LS heterodimer as formed in the crosslinking reaction. Based on the estimated molecular mass of 148 kDa, 1 mol of enzyme contained 1.0-1.6 mol of copper. Ethylxanthate, which specifically reduces CuII to CuI ethylxanthate, is a potent inhibitor of flavonol 2,4-dioxygenase. Metal chelating agents (such as diethyldithiocarbamate, diphenylthiocarbazone) strongly inhibited the enzymatic activity, but inactivation was not accompanied by loss of copper. The EPR spectrum of flavonol 2,4-dioxygenase (as isolated) showed the characteristic parameters of a nonblue type 2 CuII protein. The Cu2+ is assumed to interact with four nitrogen ligands, and the CuII complex has a (distorted) square planar geometry.     

Effect of inoculant strain and organic matter content on kinetics of 2,4-dichlorophenoxyacetic acid degradation in soil.

We monitored rates of degradation of soluble and sorbed 2,4-dichlorophenoxyacetic acid (2,4-D) in low-organic-matter soil at field capacity amended with 1, 10, or 100 micrograms of 2,4-D per g of wet soil and inoculated with one of two bacterial strains (MI and 155) with similar maximum growth rates (mu max) but significantly different half-saturation growth constants (Ks). Concentrations of soluble 2,4-D were determined by analyzing samples of pore water pressed from soil, and concentrations of sorbed 2,4-D were determined by solvent extraction. Between 65 and 75% of the total 2,4-D was present in the soluble phase at equilibrium, resulting in soil solution concentrations of ca. 8, 60, and 600 micrograms of 2,4-D per ml, respectively. Soluble 2,4-D was metabolized preferentially; this was followed by degradation of both sorbed (after desorption) and soluble 2,4-D. Rates of degradation were comparable for the two strains at soil concentrations of 10 and 100 micrograms of 2,4-D per g; however, at 1 microgram/g of soil, 2,4-D was metabolized more rapidly by the strain with the lower Ks value (strain MI). We also monitored rates of biodegradation of soluble and sorbed 2,4-D in high-organic-matter soil at field capacity amended with 100 micrograms of 2,4-D per g of wet soil and inoculated with the low-Ks strain (strain MI). Ten percent of total 2,4-D was present in the soluble phase, resulting in a soil solution concentration of ca. 30 micrograms of 2,4-D per ml.(ABSTRACT TRUNCATED AT 250 WORDS)     

Degradation of chlorobiphenyls catalyzed by the bph-encoded biphenyl-2,3-dioxygenase and biphenyl-2,3-dihydrodiol-2,3-dehydrogenase of Pseudomonas sp. LB400

Abstract In order to characterize the metabolites produced in vivo by biphenyl-2,3-dioxygenase and biphenyl-2,3-dihydrodiol-2,3-dehydrogenase, the first two enzymes of the (polychloro)biphenyl catabolic pathway encoded by the bph locus of Pseudomonas sp. LB400, recombinant E. coli strains expressing the respective genes were constructed. Biphenyl-2,3-dioxygenase attack on 2,2'- or 2,4'-dichlorobiphenyl was shown to give rise to virtually quantitative ortho -dechlorination of these congeners by hydroxylation at the chlorinated carbon 2 and its unsubstituted neighbour. Elimination of hydrochloric acid directly leads to 2,3-dihydroxy-chlorobiphenyls and obviates the need for biphenyl-2,3-dihydrodiol-2,3-dehydrogenase for the catabolism of such congeners.     

Growth on dichlorobiphenyls with chlorine substitution on each ring by bacteria isolated from contaminated African soils

Until recently, it was generally believed that the presence of more than one chlorine substituent prevented chlorinated biphenyls from serving as a sole source of carbon and energy for aerobic bacteria. In this study, we report the isolation of three aerobic strains, identified as Enterobacter sp. SA-2, Ralstonia sp. SA-4, and Pseudomonas sp. SA-6 from Nigerian polluted soils, that were able to grow on a wide range of dichlorobiphenyls (diCBs). In addition to growing on all monochlorobiphenyls (monoCBs), the strains were all able to utilize 2,2′-, 2,4′-, and 2,3-diCB as a sole source of carbon and energy. With the exception of strain SA-2, growth was also sustainable on 3,3′-, and 3,5-diCB. Washed benzoate-grown cells were typically able to degrade 68 to 100% of the diCB (100 ppm) within 188 h, concomitant with a cell number increase of up to three orders-of-magnitude and elimination of varying amounts of chloride. In many cases, stoichiometric production of a chlorobenzoate (CBA) as a product was observed. During growth on 2,2′-, and 2,4′-diCB, organisms exclusively attacked an o-chlorinated ring resulting in the production of 2-CBA and 4-CBA, respectively. A gradual decline in the concentration of the latter was observed, which suggested that the product was being degraded further. In the case of 2,3-diCB, the unsubstituted ring was preferentially metabolized. Initial diCB degradation rates were greatest for 2,4′-diCB (11.2 ± 0.91 to 30.3 ± 7.8 nmol/min per 10⁹ cells) and lowest for 2,2′-diCB (0.37 ± 0.12 to 2.7 ± 1.2 nmol/min per 10⁹ cells).     

Construction and characterization of two recombinant bacteria that grow on ortho- and para-substituted chlorobiphenyls

Cloning and expression of the aromatic ring dehalogenation genes in biphenyl-growing, polychlorinated biphenyl (PCB)-cometabolizing Comamonas testosteroni VP44 resulted in recombinant pathways allowing growth on ortho- and para-chlorobiphenyls (CBs) as a sole carbon source. The recombinant variants were constructed by transformation of strain VP44 with plasmids carrying specific genes for dehalogenation of chlorobenzoates (CBAs). Plasmid pE43 carries the Pseudomonas aeruginosa 142 ohb genes coding for the terminal oxygenase (ISPOHB) of the ortho-halobenzoate 1,2-dioxygenase, whereas plasmid pPC3 contains the Arthrobacter globiformis KZT1 fcb genes, which catalyze the hydrolytic para-dechlorination of 4-CBA. The parental strain, VP44, grew only on low concentrations of 2- and 4-CB by using the products from the fission of the nonchlorinated ring of the CBs (pentadiene) and accumulated stoichiometric amounts of the corresponding CBAs. The recombinant strains VP44(pPC3) and VP44(pE43) grew on, and completely dechlorinated high concentrations (up to 10 mM), of 4-CBA and 4-CB and 2-CBA and 2-CB, respectively. Cell protein yield corresponded to complete oxidation of both biphenyl rings, thus confirming mineralization of the CBs. Hence, the use of CBA dehalogenase genes appears to be an effective strategy for construction of organisms that will grow on at least some congeners important for remediation of PCBs.     

Aerobic mineralization of chlorobenzoates by a natural polychlorinated biphenyl-degrading mixed bacterial culture

A natural mixed aerobic bacterial culture, designated MIXE1, was found to be capable of degrading several low-chlorinated biphenyls when 4-chlorobiphenyl was used as a co-substrate. MIXE1 was capable of using all the three monochlorobenzoate (CBA) isomers tested as well as 2,5-, 3,4- and 3,5-dichlorobenzoate (dCBA) as the sole carbon and energy source. During MIXE1 growth on these substrates, a nearly stoichiometric amount of chloride was released: 0.5 g/l of each chlorobenzoate was completely mineralized by MIXE1 after 2 or 3 days of culture incubation. Two strains, namely CPE2 and CPE3, were selected from MIXE1: CPE2, referred to the Pseudomonas genus, was found to be capable of totally degrading both 2-CBA and 2,5-dCBA, whereas Alcaligenes strain CPE3 was capable of mineralizing 3-, 4-CBA and 3,4-dCBA. Substrate uptake studies carried out with whole cells of strain CPE2 suggested that 2-CBA was metabolized through catechol, while 2,5-dCBA was degraded via 4-chlorocatechol. 3-CBA, 4-CBA, and 3,4-dCBA appeared to be degraded through 3,4-dihydroxybenzoate by the CPE3 strain. MIXE1, which is capable of degrading several chlorobenzoates, should therefore be able to mineralize a number of low-chlorinated congeners of simple and complex polychlorinated biphenyl mixtures. Correspondence to: F. Fava