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Fluoroaromatics are widely and--in recent years--increasingly used as agrochemicals, starting materials for chemical syntheses and especially pharmaceuticals. This originates from the special properties the carbon-fluorine bond is imposing on organic molecules. Hence, fluoro-substituted compounds more and more are considered to be important potential environmental contaminants. On the other hand, the microbial potentials for their transformation and mineralization have received less attention in comparison to other haloaromatics. Due to the high electronegativity of the fluorine atom, its small size, and the extraordinary strength of the C-F bond, enzymes and mechanisms known to facilitate the degradation of chloro- or bromoarenes are not necessarily equally active with fluoroaromatics. Here, we review the literature on the microbial degradation of ring and side-chain fluorinated aromatic compounds under aerobic and anaerobic conditions, with particular emphasis being placed on the mechanisms of defluorination reactions.

A halobenzene-degrading bacterium, Burkholderia fungorum FLU100 (DSM 23736), was isolated due to its outstanding trait to degrade fluorobenzene. Besides fluorobenzene, it utilizes, even in random mixtures, chlorobenzene, bromobenzene, iodobenzene, benzene, and toluene as sole sources of carbon and energy. FLU100 mineralizes mono-halogenated benzenes almost stoichiometrically (according to halide balance); after a lag phase, it also degrades 3-fluorophenol and 3-chlorophenol completely. The FLU100-derived transposon Tn5-mutant FLU100-P14R22 revealed 3-halocatechol to be a central metabolite of this new halobenzene degradation pathway. In FLU100, halocatechols are-as expected-strictly subject to ortho-cleavage of the catechol ring, with meta-cleavage never been observed. The strain is able to completely mineralize 3-fluorocatechol, the principal catecholic metabolite being nearly exclusively formed from fluorobenzene. The temporarily excreted 2-fluoromuconate formed thereof in turn is subsequently metabolized completely. This important finding falsifies the customary opinion of the persistence of 2-fluoromuconate valid up to now. The degradation of 4-fluorocatechol, however, being a very minor intermediate in FLU100, is substantially slower and incomplete and leads to the accumulation of uncharacterized derivatives of muconic acid and muconolactone in the medium. This branch therefore does not seem to be productive. To our knowledge, this represents the first example of the complete metabolism of 3-fluorocatechol via 2-fluoromuconate, a metabolite hitherto described as a dead-end metabolite in fluoroaromatic degradation.

A strain Rhodococcus sp. OCT 10 DSM 45596(T), exhibiting 99.9% of 16S rDNA identity with Rhodococcus wratislaviensis NCIMB 13082, was isolated from a soil sample. The strain completely mineralised 2-chlorotoluene, 2-bromotoluene, o-xylene, benzyl alcohol and benzoate. In contrast, 2-fluorotoluene was only partially mineralised. By GC-MS and (1)H-NMR analyses, 4-chloro-3-methylcatechol was identified as the central intermediate in the degradation pathway of 2-chlorotoluene. It was further degraded by enzymes of the meta cleavage pathway. Catechol 1,2-dioxygenase and chlorocatechol 1,2-dioxygenase as the initial enzymes of the ortho cleavage pathways were not detectable under these conditions. Furthermore, neither formation nor oxidation of 2-chlorobenzylic alcohol, 2-chlorobenzaldehyde, or 2-chlorobenzoate was observed, thereby excluding side chain oxidation activity.

The effects of pH on the growth of Mycobacterium vanbaalenii PYR-1 and its degradation of phenanthrene and pyrene were compared at pH 6.5 and pH 7.5. Various degradation pathways were proposed in this study, based on the identification of metabolites from mass and NMR spectral analyses. In tryptic soy broth, M. vanbaalenii PYR-1 grew more rapidly at pH 7.5 (mu'=0.058 h(-1)) than at pH 6.5 (mu'=0.028 h(-1)). However, resting cells suspended in phosphate buffers with the same pH values displayed a shorter lag time for the degradation of phenanthrene and pyrene at pH 6.5 (6 h) than at pH 7.5 (48 h). The one-unit pH drop increased the degradation rates four-fold. Higher levels of both compounds were detected in the cytosol fractions obtained at pH 6.5. An acidic pH seemed to render the mycobacterial cells more permeable to hydrophobic substrates. The major pathways for the metabolism of phenanthrene and pyrene were initiated by oxidation at the K-regions. Phenanthrene-9,10- and pyrene-4,5-dihydrodiols were metabolized via transient catechols to the ring fission products, 2,2'-diphenic acid and 4,5-dicarboxyphenanthrene, respectively. The metabolic pathways converged to form phthalic acid. At pH 6.5, M. vanbaalenii PYR-1 produced higher levels of the O-methylated derivatives of non-K-region phenanthrene- and pyrene-diols. Other non-K-region products, such as cis-4-(1-hydroxynaphth-2-yl)-2-oxobut-3-enoic acid, 1,2-dicarboxynaphthalene and benzocoumarin-like compounds, were also detected in the culture fluids. The non-K-region polycyclic aromatic hydrocarbon oxidation might be a significant burden to the cell due to the accumulation of toxic metabolites.

1,1-Dichloro-2,2-bis(p-chlorophenyl)ethylene (DDE) is the peri-chlorinated derivative of 1,1-diphenylethylene (DPE). Biodegradation of DDE and DPE by bacteria has so far not been shown. Pure cultures of aerobic bacteria involved in biodegradation of styrene and polychlorinated biphenyls (PCB) were therefore screened for their ability to degrade or cometabolize DPE and DDE. Styrene-metabolizing bacteria (Rho-dococcus strains S5 and VLB150) grew with DPE as their sole source of carbon and energy. Polychlorinated-biphenyl-degrading bacteria (Pseudomonas fluorescens and Rhodococcus globerulus) were unable to degrade DPE even in the presence of an easily utilizable cosubstrate, biphenyl. This is the first report of the utilization of DPE as sole carbon and energy source by bacteria. All the tested bacteria failed to degrade DDE when it was provided as the sole carbon source or in the presence of the respective degradable cosubstrates. DPE transformation could also be detected in cell-free extracts of Rhodococcus S5 and VLB150, but DDE was not transformed, indicating that cell wall and membrane diffusion barriers were not limiting biodegradation. The results of the present study show that, at least for some bacteria, the chlorination of DDE is the main reason for its resistance to biodegradation by styrene and DPE-degrading bacteria.

Sixteen bacterial strains capable of degrading alkylbenzenes and alkylphenols were directly isolated from soil and water. The degradation pathways are discussed. Alkylcatechols are almost exclusively cleaved via meta-ring fission. Meta-cleavage of 3-trifluoromethyl-(TFM)-catechol was observed with all strains at different rates although the reaction rates compared to catechol as a substrate varied considerably. All 2-hydroxy-6-oxohepta-2,4-dienoic acid hydrolases investigated showed strong binding of 7,7,7-trifluoro-2-hydroxy-6-oxohepta-2,4-dienoic acid, the ring fission product of 3-TFM-catechol. Turnover rates, however, were negligible indicating this compound to be a general dead-end metabolite during metabolism of TFM-substituted compounds via meta-cleavage pathways.