Bacterial degradation of aromatic compounds

The bacterial degradation of catechol, 3-methylcatechol, 2,3-dihydroxy-β-phenylpropionic acid, and protocatechuic acid has been studied in detail. From the results obtained a general sequence has been proposed for the microbial oxidation of dihydroxy aromatic compounds.     

Cometabolic degradation of chlorinated aromatic compounds

The degradation of chlorobenzene was investigated with the specially chosen strain Methylocystis sp. GB 14 DSM 12955, using 23 ml headspace vials and in a soil column filled with quaternary aquifer material from a depth of 20 m. A long-term experiment was carried out in this column, situated in a mobile test unit at a contaminated location in Bitterfeld (Germany). Groundwater polluted by chlorobenzene was continuously fed through the column, through which a mixture comprising 4% CH(4) and 96% air was bubbled. Chlorobenzene was oxidized by up to 80% under pure culture conditions in the model experiments and was completely degraded under the mixed culture conditions of the column experiments. Over a period of 4 months, the stability of the biological system was monitored regularly by analyzing the sMMO activity as well as by classical microbiological and molecular biological methods.     

Anaerobic degradation of halogenated aromatic compounds

Recent microbiological findings show how compounds, regarded hitherto as unusual substrates for anaerobic bacteria, are degraded under anaerobic conditions. The complete conversion of halobenzoic acids and halophenolic compounds to methane by lake sediment and sewage sludge microorganisms has been demonstrated. Since haloaromatic compounds are widely used and may be found in such effluents as those from the forest industry, these studies could stimulate a broader interest in anaerobic treatment of industrial waste waters which contain unusual organic compounds.     

Anaerobic degradation of fluorinated aromatic compounds

Anaerobic enrichment cultures with sediment from an intertidal strait as inoculum were established under denitrifying, sulfate-reducing, iron-reducing and methanogenic conditions to examine the biodegradation of mono-fluorophenol and mono-fluorobenzoate isomers. Both phenol and benzoate were utilized within 2–6 weeks under all electron-accepting conditions. However, no degradation of the fluorophenols was observed within 1 year under any of the anaerobic conditions tested. Under denitrifying conditions, 2-fluorobenzoate and 4-fluorobenzoate were depleted within 84 days and 28 days, respectively. No loss of 3-fluorobenzoate was observed. All three fluorobenzoate isomers were recalcitrant under sulfate-reducing, iron-reducing, and methanogenic conditions. The degradation of the fluorobenzoate isomers under denitrifying conditions was examined in more detail using soils and sediments from different geographic regions around the world. Stable enrichment cultures were obtained on 2-fluorobenzoate or 4-fluorobenzoate with inoculum from most sites. Fluoride was released stoichiometrically, and nitrate reduction corresponded to the values predicted for oxidation of fluorobenzoate to CO₂ coupled to denitrification. The 2-fluorobenzoate-utilizing and 4-fluorobenzoate-utilizing cultures were specific for fluorobenzoates and did not utilize other halogenated (chloro-, bromo-, iodo-) benzoic acids. Two denitrifying strains were isolated that utilized 2-fluorobenzoate and 4-fluorobenzoate as growth substrates. Preliminary characterization indicated that the strains were closely related to Pseudomonas stutzeri. Received: 1 September 1999 / Accepted in revised form: 30 September 1999     

Metabolic diversity in bacterial degradation of aromatic compounds

Aromatic compounds pose a major threat to the environment, being mutagenic, carcinogenic, and recalcitrant. Microbes, however, have evolved the ability to utilize these highly reduced and recalcitrant compounds as a potential source of carbon and energy. Aerobic degradation of aromatics is initiated by oxidizing the aromatic ring, making them more susceptible to cleavage by ring-cleaving dioxygenases. A preponderance of aromatic degradation genes on plasmids, transposons, and integrative genetic elements (and their shuffling through horizontal gene transfer) have lead to the evolution of novel aromatic degradative pathways. This enables the microorganisms to utilize a multitude of aromatics via common routes of degradation leading to metabolic diversity. In this review, we emphasize the exquisiteness and relevance of bacterial degradation of aromatics, interlinked degradative pathways, genetic and metabolic regulation, carbon source preference, and biosurfactant production. We have also explored the avenue of metagenomics, which opens doors to a plethora of uncultured and uncharted microbial genetics and metabolism that can be used effectively for bioremediation.     

Bacterial degradation of aromatic compounds via angular dioxygenation

Dioxygenation is one of the important initial reactions of the bacterial degradation of various aromatic compounds. Aromatic compounds, such as biphenyl, toluene, and naphthalene, are dioxygenated at lateral positions of the aromatic ring resulting in the formation of cis-dihydrodiol. This "normal" type of dioxygenation is termed lateral dioxygenation. On the other hand, the analysis of the bacterial degradation of fluorene (FN) analogues, such as 9-fluorenone, dibenzofuran (DF), carbazole (CAR), and dibenzothiophene (DBT)-sulfone, and DF-related diaryl ether compounds, dibenzo-p-dioxin (DD) and diphenyl ether (DE), revealed the presence of the novel mode of dioxygenation reaction for aromatic nucleus, generally termed angular dioxygenation. In this atypical dioxygenation, the carbon bonded to the carbonyl group in 9-fluorenone or to heteroatoms in the other compounds, and the adjacent carbon in the aromatic ring are both oxidized. Angular dioxygenation of DF, CAR, DBT-sulfone, DD, and DE produces the chemically unstable hemiacetal-like intermediates, which are spontaneously converted to 2,2',3-trihydroxybiphenyl, 2'-aminobiphenyl-2,3-diol, 2',3'-dihydroxybiphenyl-2-sulfinate, 2,2',3-trihydroxydiphenyl ether, and phenol and catechol, respectively. Thus, angular dioxygenation for these compounds results in the cleavage of the three-ring structure or DE structure. The angular dioxygenation product of 9-fluorenone, 1-hydro-1,1a-dihydroxy-9-fluorenone is a chemically stable cis-diol, and is enzymatically transformed to 2'-carboxy-2,3-dihydroxybiphenyl. 2'-Substituted 2,3-dihydroxybiphenyls formed by angular dioxygenation of FN analogues are degraded to monocyclic aromatic compounds by meta cleavage and hydrolysis. Thus, after the novel angular dioxygenation, subsequent degradation pathways are homologous to the corresponding part of that of biphenyl. Compared to the bacterial strains capable of catalyzing lateral dioxygenation, few bacteria having angular dioxygenase have been reported. Only a few degradation pathways, CAR-degradation pathway of Pseudomonas resinovorans strain CA10, DF/DD-degradation pathway of Sphingomonas wittichii strain RW1, DF/DD/FN-degradation pathway of Terrabacter sp. strain DBF63, and carboxylated DE-degradation pathway of P. pseudoalcaligenes strain POB310, have been investigated at the gene level. As a result of the phylogenetic analysis and the comparison of substrate specificity of angular dioxygenase, it is suggested that this atypical mode of dioxygenation is one of the oxygenation reactions originating from the relaxed substrate specificity of the Rieske nonheme iron oxygenase superfamily. Genetic characterization of the degradation pathways of these compounds suggests the possibility that the respective genetic elements constituting the entire catabolic pathway have been recruited from various other bacteria and/or other genetic loci, and that these pathways have not evolutionary matured.     

Microbial degradation of recalcitrant compounds and synthetic aromatic polymers

The evolution of microbial catabolic enzymes cannot keep pace with the rapid introduction of novel compounds into the environment. These new synthetic compounds that are slowly biodegradable or non-biodegradable are known as recalcitrant compounds, and range from simple halogenated hydrocarbons to complex polymers. Recalcitrant compounds can be made biodegradable by developing microorganisms capable of degrading the compound and by treating the compound to make it more conducive to mirobial attack. Many factors contribute to recalcitrance. The organism may lack the necessary genetic information. The organism can acquire this information by plasmid transfer or de novo enzyme synthesis. Plasmids have been characterized that degrade or transform antibiotics, pesticides, and hydrocarbons. By the use of chemostat techniques or chemical mutagens, organisms have been shown to synthesize de novo enzymes. The compound may be too large to enter the cell, or a transport system may not exist to transport it across the membrane. The compound may be insoluble, either as a solid or a liquid, and the microorganism may lack the proper nutrients. Recalcitrant compounds can be oxygenated prior to degradation, in the presence of a readily assimilable carbon source. In the absence of the assimilable carbon source, the recalcitrant compound is not degraded, or only very slowly. Examples of such co-oxidative metabolism are alkane and lignin degradation. Polymers, particularly synthetic ones, are prime examples of difficult-to-degrade compounds. The initial rate of polymer degradation follows a Freundlich or modified Langmuir isotherm rather than Michaelis-Menten kinetics. Microorganisms can irreversibly bind to solid surfaces by various methods. Soil microorganisms have been found to degrade styrene monomers and dimers. Polystyrene has been shown to be biodegradable by ¹⁴CO₂ evolution but at a very slow rate. In car tyres, styrene as a copolymer of butadiene is co-metabolized in the presence of other assimilable carbon sources.     

Epoxy coenzyme a thioester pathways for degradation of aromatic compounds

Aromatic compounds (biogenic and anthropogenic) are abundant in the biosphere. Some of them are well-known environmental pollutants. Although the aromatic nucleus is relatively recalcitrant, microorganisms have developed various catabolic routes that enable complete biodegradation of aromatic compounds. The adopted degradation pathways depend on the availability of oxygen. Under oxic conditions, microorganisms utilize oxygen as a cosubstrate to activate and cleave the aromatic ring. In contrast, under anoxic conditions, the aromatic compounds are transformed to coenzyme A (CoA) thioesters followed by energy-consuming reduction of the ring. Eventually, the dearomatized ring is opened via a hydrolytic mechanism. Recently, novel catabolic pathways for the aerobic degradation of aromatic compounds were elucidated that differ significantly from the established catabolic routes. The new pathways were investigated in detail for the aerobic bacterial degradation of benzoate and phenylacetate. In both cases, the pathway is initiated by transforming the substrate to a CoA thioester and all the intermediates are bound by CoA. The subsequent reactions involve epoxidation of the aromatic ring followed by hydrolytic ring cleavage. Here we discuss the novel pathways, with a particular focus on their unique features and occurrence as well as ecological significance.     

The anaerobic degradation of aromatic compounds by a denitrifying bacterium

Summary Six strains of Rhizobium, present as bacteroids, in Lotus nodules were studied by electron microscopy. Three inclusion bodies frequently detected are described and their distribution among the strains is given. Cytochemical techniques indicated that they have, as principal components, polyphosphate, lipid and neutral polysaccharide, probably glycogen, respectively.     

Aerobic bacterial degradation of polycyclic aromatic hydrocarbons (PAHs) and its kinetic aspects

Aerobic bacterial degradation of PAHs is reviewed. Particular attention is paid to its kinetic aspects (rate and specificity). The general concepts of PAH biodegradation in nature and the role of aerobic bacteria in this process are described. The problem of PAH bioavailability and the mechanism of PAH penetration through bacterial cell wall are discussed. The key role of the reaction of PAH hydroxylation in controlling the rate and specificity of PAH biodegradation process is substantiated. The effects of competitive inhibition, intermediate inhibition, cross induction, and cometabolism are considered. The importance of microbial communities for PAH biodegradation in natural ecosystems is shown. The review contains the list of 138 references.     

Microbial degradation of aromatic compounds - from one strategy to four

Aromatic compounds are both common growth substrates for microorganisms and prominent environmental pollutants. The crucial step in their degradation is overcoming the resonance energy that stabilizes the ring structure. The classical strategy for degradation comprises an attack by oxygenases that hydroxylate and finally cleave the ring with the help of activated molecular oxygen. Here, we describe three alternative strategies used by microorganisms to degrade aromatic compounds. All three of these methods involve the use of CoA thioesters and ring cleavage by hydrolysis. However, these strategies are based on different ring activation mechanisms that consist of either formation of a non-aromatic ring-epoxide under oxic conditions, or reduction of the aromatic ring under anoxic conditions using one of two completely different systems.     

Stereospecific enzymes in the degradation of aromatic compounds by pseudomonas putida

Two reactions in the catabolism of catechol by meta-fission, namely, hydration of 2-oxopent-4-enoate (vinylpyruvate) and aldol fission of the product, are catalyzed by stereospecific enzymes. The absolute configuration of this hydration product was shown to be l(S)-4-hydroxy-2-oxopentanoate. Vinylpyruvate hydratase, purified almost to homogeneity, had a molecular weight of about 287,000 and was dissociated in sodium dodecyl sulfate, without prior treatment with mercaptoethanol, into a species with an approximate molecular weight of 28,000. The hydratase was highly specific for its substrates; thus, although 2-oxo-cis-hex-4-enoate was also hydrated, structurally similar compounds such as the trans isomer, vinylacetic and crotonic acids, and the ring-fission products of catechol and methylcatechols were not attacked. Vinylpyruvate hydratase was activated by Mn(2+) ions. On the basis of these observations, a mechanism is proposed which closely resembles that for 4-hydroxy-2-oxopentanoate aldolase. A possible evolutionary connection between functionally related, divalent cation-activated hydro-lyases and aldolases is discussed. It was also demonstrated that l-(S)-4-hydroxy-2-oxohexanoate is the biologically active enantiomer of this hydroxy acid.     

Methanogenic degradation of (amino)aromatic compounds by anaerobic microbial communities

degradation of a range of aromatic substrates by anaerobic microbial communities was studied. Active methanogenic microbial communities decomposing aminoaromatic acids and azo dyes into CH₄ and CO₂ were isolated. Products of primary conversion were found to be 2-hydroxybenzyl and benzyl alcohols gradually transforming into benzoate. It was shown that isolated microbial communities are capable of converting the initial substrates—benzyl alcohol, benzoate, salicylic acid, and azo dye Acid Orange 6—into biogas without a lag-phase but with different velocities. Aromatic and linear intermediates of biodegradation of aromatic amines by obtained enrichment cultures were determined for the first time. Selective effect of aromatic substrates on a microbial community that was expressed in decrease in diversity and gradual change of dominant morphotypes was revealed.