Degradation of 4-Chlorobenzoic Acid by
            <i>Arthrobacter</i>
            sp

Marks, Trevor S.; Smith, Andrew; Quirk, Alan V.

doi:10.1128/aem.48.5.1020-1025.1984

Cited by 127 publications

(49 citation statements)

References 14 publications

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“…Arthrobacter sp. strain TM-1 was able to dehalogenate 4-chloro-, 4-bromo-and 4-fluorobenzoate, but only 4-chlorobenzoate supported growth [230]. The dehalogenase of the Pseudomonas sp.…”

Section: Aerobic Degradation Of Halobenzoatesmentioning

confidence: 99%

Microbial breakdown of halogenated aromatic pesticides and related compounds

Häggblom

1992

FEMS Microbiology Letters

363

132

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Considerable progress has been made in the last few years in understanding the mechanisms of microbial degradation of halogenated aromatic compounds. Much is already known about the degradation mechanisms under aerobic conditions, and metabolism under anaerobiosis has lately received increasing attention. The removal of the halogen substituent is a key step in degradation of halogenated aromatics. This may occur as an initial step via reductive, hydrolytic or oxygenolytic mechanisms, or after cleavage of the aromatic ring at a later stage of metabolism. In addition to degradation, several biotransformation reactions, such as methylation and polymerization, may take place and produce more toxic or recalcitrant metabolites. Studies with pure bacterial and fungal cultures have given detailed information on the biodegradation pathways of several halogenated aromatic compounds. Several of the key enzymes have been purified or studied in cell extracts, and there is an increasing understanding of the organization and regulation of the genes involved in haloaromatic degradation. This review will focus on the biodegradation and biotransformation pathways that have been established for halogenated phenols, phenoxyalkanoic acids, benzoic acids, benzenes, anilines and structurally related halogenated aromatic pesticides. There is a growing interest in developing microbiological methods for clean‐up of soil and water contaminated with halogenated aromatic compounds.

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“…Arthrobacter sp. strain TM-1 was able to dehalogenate 4-chloro-, 4-bromo-and 4-fluorobenzoate, but only 4-chlorobenzoate supported growth [230]. The dehalogenase of the Pseudomonas sp.…”

Section: Aerobic Degradation Of Halobenzoatesmentioning

confidence: 99%

Microbial breakdown of halogenated aromatic pesticides and related compounds

Häggblom

1992

FEMS Microbiology Letters

363

132

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“…TM-I (MARKS et al 1984b), it was shown that the novel hydroxyl group was derived from water. 4-hydroxybenzoate was subsequently hydroxylated to 3,4-dihydroxybenzoate (KLA- GES and LINGENS 1979, MARKS et al 1984a, RUISINGER et al 1976, VAN DEN TWEEL et al 1986) and cleaved either by the orrho pathway to cis,&-muconic acid (KLAGES and LINGENS , RUISINGER et al 1976 or by the meta pathway to 2-hydroxy-4carboxymuconic acid semialdehyde ( KLAGES and LINGENS 1979).…”

Section: Hydroxylationdechlorinationmentioning

confidence: 99%

Mechanisms of bacterial degradation and transformation of chlorinated monoaromatic compounds

Häggblom

1990

J. Basic Microbiol.

115

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Chloroaromatics are xenobiotic compounds of environmental concern. They can be removed from the environment by (bio)degradation or by (bio)transformation. Recognition of the mechanisms and requirements of their biodegradation is of cardinal importance for understanding the fate of these chemicals in the environment, and for developing methods for biological treatment of wastes containing compounds of this type. Cleavage of the carbon-halogen bond is the critical step in degradation of chloroaromatics. As exemplified with chlorophenols, chlorobenzoates and chlorobenzenes in this review, two distinct strategies are employed by bacteria for degradation of chlorinated aromatic compounds: the particular chlorine substituents are removed either directly from the aromatic ring (as an initial step in degradation) or after oxygenative ring cleavage (from chlorinated aliphatic intermediates). Direct elimination of chlorine substituents from the aromatic ring occurs by displacement with either hydroxyl groups (hydrolytically or oxygenolytically) or hydrogen atoms (reductive dechlorination). Dechlorinations of the latter type require reducing power and are significant in anaerobic environments, but have also been observed with strictly aerobic bacteria. Various biotransformation reactions, with only minor alteration of the parent compound, are an alternative to biogradation. Two environmentally significant transformation reactions discussed here are O-methylation and O-demethylation. The capability to O-methylate chlorinated hydroxybenzenes seems to be widespread in bacteria. O-Methylation is an environmentally important transformation reaction, since methylation increases the lipophilicity of the compound and thus the potential for bioaccumulation. Bacterial O-demethylation of chlorinated methoxylated compounds has been observed under both aerobic and anaerobic conditions.

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“…[126]: even the anaerobic degradation of guanine involves two separate sets of three hydrolases each [132]. Furthermore, reports of hydrolytic dechlorinations at an aromatic ring are still rare [133,134] compared with occasional oxidative dehalogenation and the more frequent dehalogenation subsequent to ring cleavage [135], and with the reductire reactions [77,136]. The hydrolytic reactions at the aromatic s-triazine ring are facilitated by the incomplete delocalisation of the ~r-electrons [112], which results in a low electron density at the carbon atoms and susceptibility to nucleophilic attack.…”

Section: Summing Upmentioning

confidence: 99%

Biodegration of s-triazine xenobiotics

Cook

1987

FEMS Microbiology Letters

206

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SUMMARYBiodegradation of xenobiotic compounds is examined with s-triazines as an example and with biological treatment of wastewater containing striazines as an aim. s-Triazines have been termed recalcitrant, but examination of the literature indicates that a potential for biodegradation exists. Nitrogen-limited enrichment cultures yield organisms able to degrade by-products of the industrial synthesis of s-triazine herbicides as sources of nitrogen. The choice of inoculum for these enrichments is important and often allows for successful enrichment after simple batch culture, but organisms containing several degradative reactions could be obtained only after selection in extended culture. Routine, specific determinations of all s-triazines (by HPLC) were essential throughout the work. Molar growth yields show complete mass balances for the utilization of s-triazines. Kinetic experiments indicate that specific degradation rates of s-triazines in growing cells are about 0.4 mkat/kg of protein. Characterised biochemical pathways consist of a series of hydrolytic cleavages of chloro-, amino-and alkylaminogroups from the s-triazine ring. Pathways con-

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Degradation of 4-Chlorobenzoic Acid by Arthrobacter sp

Cited by 127 publications

References 14 publications

Microbial breakdown of halogenated aromatic pesticides and related compounds

Microbial breakdown of halogenated aromatic pesticides and related compounds

Mechanisms of bacterial degradation and transformation of chlorinated monoaromatic compounds

Biodegration of s-triazine xenobiotics

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