Microbial degradation of chlorinated phenols

Chlorophenols have been introduced into the environment through their use as biocides and as by-products of chlorine bleaching in the pulp and paper industry. Chlorophenols are subject to both anaerobic and aerobic metabolism. Under anaerobic conditions, chlorinated phenols can undergo reductive dechlorination when suitable electron-donating substrates are available. Halorespiring bacteria are known which can use both low and highly chlorinated congeners of chlorophenol as electron acceptors to support growth. Many strains of halorespiring bacteria have the capacity to eliminate ortho-chlorines; however only bacteria from the species Desulfitobacterium hafniense (formerly frappieri) can eliminate para- and meta-chlorines in addition to ortho-chlorines. Once dechlorinated, the phenolic carbon skeletons are completely converted to methane and carbon dioxide by other anaerobic microorganisms in the environment. Under aerobic conditions, both lower and higher chlorinated phenols can serve as sole electron and carbon sources supporting growth. The best studied strains utilizing pentachlorophenol belong to the genera Mycobacterium and Sphingomonas. Two main strategies are used by aerobic bacteria for the degradation of chlorophenols. Lower chlorinated phenols for the most part are initially attacked by monooxygenases yielding chlorocatechols as the first intermediates. On the other hand, polychlorinated phenols are converted to chlorohydroquinones as the initial intermediates. Fungi and some bacteria are additionally known that cometabolize chlorinated phenols.     

Microbial degradation of chlorinated benzenes

Chlorinated benzenes are important industrial intermediates and solvents. Their widespread use has resulted in broad distribution of these compounds in the environment. Chlorobenzenes (CBs) are subject to both aerobic and anaerobic metabolism. Under aerobic conditions, CBs with four or less chlorine groups are susceptible to oxidation by aerobic bacteria, including bacteria (Burkholderia, Pseudomonas, etc.) that grow on such compounds as the sole source of carbon and energy. Sound evidence for the mineralization of CBs has been provided based on stoichiometric release of chloride or mineralization of (14)C-labeled CBs to (14)CO(2). The degradative attack of CBs by these strains is initiated with dioxygenases eventually yielding chlorocatechols as intermediates in a pathway leading to CO(2) and chloride. Higher CBs are readily reductively dehalogenated to lower chlorinated benzenes in anaerobic environments. Halorespiring bacteria from the genus Dehalococcoides are implicated in this conversion. Lower chlorinated benzenes are less readily converted, and mono-chlorinated benzene is recalcitrant to biotransformation under anaerobic conditions.     

Microbial degradation of chlorinated acetophenones.

A defined mixed culture, consisting of an Arthrobacter sp. and a Micrococcus sp. and able to grow with 4-chloroacetophenone as a sole source of carbon and energy, was isolated. 4-Chlorophenyl acetate, 4-chlorophenol, and 4-chlorocatechol were identified as metabolites through comparison of retention times and UV spectra with those of standard substances. The proposed pathway was further confirmed by investigation of enzymes. The roles of the two collaborating strains were studied by growth experiments and on the level of enzymes. If transient accumulation of 4-chlorophenol was avoided either by the use of phenol-absorbing substances or by careful supplement of 4-chloroacetophenone, the Arthrobacter sp. was able to grow as a pure culture with 4-chloroacetophenone as a sole source of carbon and energy. Several mono-, di-, and trichlorinated acetophenones were mineralized by the Arthrobacter sp.     

Microbial transformation of chlorinated benzoates

Chlorinated benzoates enter the environment through their use as herbicides or as metabolites of other halogenated compounds. Ample evidence is available indicating biodegradation of chlorinated benzoates to CO₂ and chloride in the environment under aerobic as well as anaerobic conditions. Under aerobic conditions, lower chlorinated benzoates can serve as sole electron and carbon sources supporting growth of a large list of taxonomically diverse bacterial strains. These bacteria utilize a variety of pathways ranging from those involving an initial degradative attack by dioxygenases to those initiated by hydrolytic dehalogenases. In addition to monochlorinated benzoates, several bacterial strains have been isolated that can grow on dichloro-, and trichloro- isomers of chlorobenzoates. Some aerobic bacteria are capable of cometabolizing chlorinated benzoates with simple primary substrates such as benzoate. Under anaerobic conditions, chlorinated benzoates are subject to reductive dechlorination when suitable electron-donating substrates are available. Several halorespiring bacteria are known which can use chlorobenzoates as electron acceptors to support growth. For example, Desulfomonile tiedjei catalyzes the reductive dechlorination of 3-chlorobenzoate to benzoate. The benzoate skeleton is mineralized by other microorganisms in the anaerobic environment. Various dichloro- and trichlorobenzoates are also known to be dechlorinated in anaerobic sediments.     

Degradation of chlorinated phenols by a pentachlorophenol-degrading bacterium

A pentachlorophenol (PCP)-degrading Flavobacterium sp. was tested for its ability to dechlorinate other chlorinated phenols by using resting cells that had been grown in the presence or absence of PCP. Phenols with chlorine atoms at positions 2 and 6 of the phenol ring were dechlorinated completely by PCP-induced cells. Other chlorinated phenols were not significantly mineralized. When PCP was added to a culture growing on L-glutamate, there was a lag period before the start of PCP degradation. When similar cells were treated with chloramphenicol prior to the addition of PCP, they did not degrade added PCP, even after prolonged incubations. Thus, the enzymes necessary for PCP degradation appeared to be inducible. Suspensions of cells grown in the presence of 2,4,6-trichlorophenol or 2,3,5,6-tetrachlorophenol did not show a lag period for mineralization of PCP, 2,4,6-trichlorophenol, or 2,3,5,6-tetrachlorophenol, indicating that one enzyme system probably was induced for the biodegradation of all three compounds. Nondegradable chlorophenols were toxic toward the Flavobacterium sp., probably acting as uncouplers of oxidative phosphorylation.     

O-methylation of chlorinated phenols in the genus Rhodococcus

The ability to O-methylate chlorinated phenols and phenol derivatives in the genus Rhodococcus was studied. Several species and strains O-methylated chlorophenols to the corresponding anisoles, namely R. equi, R. erythropolis, R. rhodochrous, and Rhodococcus sp. strains P1 and An 117. The ability for a strain to O-methylate chlorophenols did not require that it had been isolated from an environment containing a chlorinated aromatic compound. O-methylation activity was stimulated by the presence of carbohydrate. All strains preferentially O-methylated a substrate with the hydroxyl group flanked by two chlorine substitunts.     

Microbial ecology of chlorinated solvent biodegradation

This study focused on the microbial ecology of tetrachloroethene (PCE) degradation to trichloroethene, cis‐1,2‐dichloroethene and vinyl chloride to evaluate the relationship between the microbial community and the potential accumulation or degradation of these toxic metabolites. Multiple soil microcosms supplied with different organic substrates were artificially contaminated with PCE. A thymidine analogue, bromodeoxyuridine (BrdU), was added to the microcosms and incorporated into the DNA of actively replicating cells. We compared the total and active bacterial communities during the 50‐day incubations by using phylogenic microarrays and 454 pyrosequencing to identify microorganisms and functional genes associated with PCE degradation to ethene. By use of this integrative approach, both the key community members and the ecological functions concomitant with complete PCE degradation could be determined, including the presence and activity of microbial community members responsible for producing hydrogen and acetate, which are critical for Dehalococcoides‐mediated PCE degradation. In addition, by correlation of chemical data and phylogenic microarray data, we identified several bacteria that could potentially oxidize hydrogen. These results demonstrate that PCE degradation is dependent on some microbial community members for production of appropriate metabolites, while other members of the community compete for hydrogen in soil at low redox potentials.     

Degradation of chlorinated phenols by a pentachlorophenol-degrading bacterium.

A pentachlorophenol (PCP)-degrading Flavobacterium sp. was tested for its ability to dechlorinate other chlorinated phenols by using resting cells that had been grown in the presence or absence of PCP. Phenols with chlorine atoms at positions 2 and 6 of the phenol ring were dechlorinated completely by PCP-induced cells. Other chlorinated phenols were not significantly mineralized. When PCP was added to a culture growing on L-glutamate, there was a lag period before the start of PCP degradation. When similar cells were treated with chloramphenicol prior to the addition of PCP, they did not degrade added PCP, even after prolonged incubations. Thus, the enzymes necessary for PCP degradation appeared to be inducible. Suspensions of cells grown in the presence of 2,4,6-trichlorophenol or 2,3,5,6-tetrachlorophenol did not show a lag period for mineralization of PCP, 2,4,6-trichlorophenol, or 2,3,5,6-tetrachlorophenol, indicating that one enzyme system probably was induced for the biodegradation of all three compounds. Nondegradable chlorophenols were toxic toward the Flavobacterium sp., probably acting as uncouplers of oxidative phosphorylation.     

Bacterial cometabolic degradation of chlorinated paraffins

Summary Cometabolic dechlorination of chlorinated paraffins was demonstrated in the presence of n-hexadecane by bacterial strains (HK-3, HK-6, HK-8, and HK-10) isolated from soil samples.Eleven per cent of chlorine of chlorinated paraffin-150 (CP-150) was released by strain HK-3. The mixed culture of strain HK-3, catalyzing the dechlorination of terminal chlorine of chloroalkane, and strain H15-4, capable of releasing the chlorine from 2-chlorinated fatty acids, dechlorinated CP-150 up to 13%. The mixed culture of the four strains (HK-3, HK-6, HK-8, and HK-10) performed the dechlorination of CP-150 by cometabolism in a jar fermentor pH at 7.0. The amount of chloride released from the chlorinated paraffins tested was in the range of 15–57%.The activated sludge acclimatized to n-hexadecane for 60 days showed a little dechlorination activity to CP-150.     

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.     

Microbial sensors for determination of aromatics and their chloroderivatives. Part II: Determination of chlorinated phenols using a Rhodococcus-containing biosensor

An amperometric biosensor for determination of phenol and chlorophenols using Rhodococcus has been developed. This sensor is more sensitive to phenol and chlorophenols, especially to mono- and dichlorinated phenol, than to benzoate and monochlorobenzoates. The incubation of the sensor with phenol and its chlorinated derivatives enhanced the activity of the microbial sensor for these compounds. A linear relationship between the current range and the concentration of phenol, 2-, 3- and 4-chlorophenol was observed up to 20 mol/l. The detection limit for all studied substrates was 4 mol/l. The current difference was reproducible within 5.5% when the test solution contained 40 mol phenol/l. Correspondence to: K. Riedel     

Utilization and cooxidation of chlorinated phenols byPseudomonas sp. B 13

Pseudomonas sp. B13 was grown in continuous culture on 4-chlorophenol as the only carbon source. Maximum growth rate of 0.4h^-1 was observed at a substrate concentration of >0.01 mM and <0.15 mM. In addition to the enzymes of phenol catabolism, high specific 1,2-dioxygenase activities with chlorocatechols as substrates were found. The isomeric monochlorinated phenols were also totally degraded by 4-chlorophenol grown cells. (+)-2,5-Dihydro-4-methyl- and (+)-2,5-dihydro-2-methyl-5-oxo-furan-2-acetic acid were formed in high yield as dead-end catabolites from cooxidation of cresoles.Several dichlorophenols except 2,6-dichlorophenol were removed from the culture fluid by chlorophenol grown cells. Ring cleavage of chlorinated catechols were shown to be one of the critical steps in chlorophenol catabolism. A catabolic pathway for isomeric chlorophenols is discussed.Non-Standard Abbreviations HPLC High performance liquid chromatography - DHB Dihydrodihydroxybenzoate 3,5-cyclohexadiene-1,2-diol-1-carboxylic acid     

Microbial degradation of pentachlorophenol

Pentachlorophenol (PCP) was the most prevalent wood preservative for many years worldwide. Its widespread use had led to contamination of various environments. Traditional methods of PCP clean-up include storage in land-fill sites, incineration and abiotic degradation processes such as photodecomposition. Some aerobic and anaerobic microorganisms can degrade PCP under a variety of conditions. Axenic bacterial cultures, Flavobacterium sp., Rhodococcus sp., Arthrobacter sp., Pseudomonas sp., Sphingomonas sp., and Mycobacterium sp., and fungal cultures, Phanerochaete sp. and Trametes sp. exhibit varying rates and extent of PCP degradation. This paper provides some general information on properties of PCP and reviews the influence of nutrient amendment, temperature and pH on PCP degradation by various aerobic and anaerobic microorganisms. Where information is available, proposed degradation pathways, intermediates and enzymes are reviewed.     

Microbial degradation of lignin

The transformations of lignin that occur during its biodegradation are complex and incompletely understood. Certain fungi of the white-rot group, and possibly other fungi and bacteria, completely decompose lignin to carbon dioxide and water. Other fungi and bacteria apparently degrade lignin incompletely. Differences in lignin-degrading abilities observed for different organisms may result from differences in the completeness of their ligninolytic enzyme systems. Not all lignin components may be attacked by a particular organism. Alternatively, different organisms may differ in their basic mechanisms of attack on lignin. The basic pathways of lignin degradation have been elucidated only for certain representatives of the white-and brown-rot fungi. Although it is known that each of the principal structural components of lignin is attacked by other fungi and bacteria, the biochemistry of that attack has not been elucidated. Work with low molecular weight lignin models has provided only limited information on possible pathways of lignin degradation by microorganisms. There is little evidence to suggest a correlation between abilities to degrade single-ring aromatic or lignin model compounds and the ability to degrade polymeric lignin. More evidence has come from analysis of spent culture media for lignin breakdown products and from comparative chemical analyses of sound lignins versus decayed lignin residues. Accumulated evidence with the most thoroughly studied white-rot fungi suggests that with these fungi lignin degradation proceeds by way of extracellular mixed-function oxygenases and dioxygenases, which catalyse demethylations, hydroxylations and ring-fission reactions within a largely intact polymer, concomitant with some release of low molecular weight lignin fragments. There are also apparent relationships between lignin, carbohydrate and nitrogen metabolism for some organisms, but the relationships may vary from one organism to another. Although research is now mostly at a basic level, industrial applications may result from lignin degradation research. Considerable potential exists for the development of bioconversions which might produce low molecular weight chemicals from waste lignins, and thereby reduce our dependence on petroleum as a source of these chemicals. Alternatively, such bioconversions might produce chemically altered forms of polymeric lignin that may be valuable industrially.     

聚乙烯塑料的微生物降解

聚乙烯(polyethylene,PE)是产量最大的通用塑料之一,通常被加工成一次性包装材料(包括塑料袋及容器)和农用薄膜等。PE塑料的广泛应用导致大量PE废弃物的累积,对生态环境造成严重的威胁。自20世纪70年代以来,一些研究陆续报道了PE塑料被微生物降解的现象,并从土壤、海洋、垃圾堆置点及昆虫肠道等生境中分离筛选到了若干种具有一定PE塑料降解能力的菌株,而且发现一些单加氧酶、过氧化物酶和漆酶等氧化还原酶对PE塑料具有氧化降解能力。这些研究为发展PE塑料废弃物生物降解处理技术提供了一定的依据。本文总结和分析了PE塑料降解微生物的分离和筛选方法,以及已报道的PE塑料降解微生物和降解酶的研究进展,以期为进一步研究PE塑料的微生物降解机理和处理技术提供参考。     

Microbial degradation of octamethylcyclotetrasiloxane

The microbial degradation of low-molecular-weight polydimethylsiloxanes was investigated through laboratory experiments. Octamethylcyclotetrasiloxane was found to be biodegraded under anaerobic conditions in composted sewage sludge, as monitored by the occurrence of the main polydimethylsiloxane degradation product, dimethylsilanediol, compared to that found in experiments with sterilized control samples.     

Microbial degradation of polyethers

This paper summarizes studies on microbial degradation of polyethers. Polyethers are aerobically metabolized through common mechanisms (oxidation of terminal alcohol groups followed by terminal ether cleavage), well-characterized examples being found with polyethylene glycol (PEG). First the polymer is oxidized to carboxylated PEG by alcohol and aldehyde dehydrogenases and then the terminal ether bond is cleaved to yield the depolymerized PEG by one glycol unit. Most probably PEG is anaerobically metabolized through one step which is catalyzed by PEG acetaldehyde lyase, analogous to diol dehydratase. Whether aerobically or anaerobically, the free OH group is necessary for metabolization of PEG. PEG with a molecular weight of up to 20,000 was metabolized either in the periplasmic space (Pseudomonas stutzeri and sphingomonads) or in the cytoplasm (anaerobic bacteria), which suggests the transport of large PEG through the outer and inner membranes of Gram-negative bacterial cells. Membrane-bound PEG dehydrogenase (PEG-DH) with high activity towards PEG 6,000 and 20,000 was purified from PEG-utilizing sphingomonads. Sequencing of PEG-DH revealed that the enzyme belongs to the group of GMC flavoproteins, FAD being the cofactor for the enzyme. On the other hand, alcohol dehydrogenases purified from other bacteria that cannot grow on PEG oxidized PEG. Cytoplasmic NAD-dependent alcohol dehydrogenases with high specificity towards ether-alcohol compound, either crude or purified, showed appreciable activity towards PEG 400 or 600. Liver alcohol dehydrogenase (equine) also oxidized PEG homologs, which might cause fatal toxic syndrome in vivo by carboxylating PEG together with aldehyde dehydrogenase when PEG was absorbed. An ether bond-cleaving enzyme was detected in PEG-utilizing bacteria and purified as diglycolic acid (DGA) dehydrogenase from a PEG-utilizing consortium. The enzyme oxidized glycolic acid, glyoxylic acid, as well as PEG-carboxylic acid and DGA. Similarly, dehydrogenation on polypropylene glycol (PPG) and polytetramethylene glycol (PTMG) was suggested with cell-free extracts of PPG and PTMG-utilizing bacteria, respectively. PPG commercially available is atactic and includes many structural (primary and secondary alcohol groups) and optical (derived from pendant methyl groups on the carbon backbone) isomers. Whether PPG dehydrogenase (PPG-DH) has wide stereo- and enantioselective substrate specificity towards PPG isomers or not must await further purification. Preliminary research on PPG-DH revealed that the enzyme was inducibly formed by PPG in the periplasmic, membrane and cytoplasm fractions of a PPG-utilizing bacterium Stenotrophomonas maltophilia. This finding indicated the intracellular metabolism of PPG is the same as that of PEG. Besides metabolization of polyethers, a biological Fenton mechanism was proposed for degradation of PEG, which was caused by extracellular oxidants produced by a brown-rot fungus in the presence of a reductant and Fe3+, although the metabolism of fragmented PEG has not yet been well elucidated.     

木质纤维素的微生物降解

木质纤维素广泛存在于自然界中,因结构复杂,其高效降解需要多种微生物的协同互作,由于参与木质纤维素降解的微生物种类繁多,其协同降解机理尚不完全明确。随着微生物分子生物学和组学技术的快速发展,将为微生物协同降解木质纤维素机制的研究提供新的方法和思路。笔者前期研究发现,细菌复合菌系在50℃下表现出强大的木质纤维素降解能力,菌系由可分离培养和暂时不可分离培养细菌组成,但是可分离培养细菌没有降解能力。通过宏基因组和宏转录组研究表明,与木质纤维素降解相关的某些基因表达量发生显著变化,通过组学方法有可能更加深入解释微生物协同降解木质纤维素的微生物学和酶学机理。文中从酶、纯培养菌株和复合菌群三个方面综述了木质纤维素微生物降解研究进展,着重介绍了组学技术在解析复合菌群作用机理方面的现状和应用前景,以期为探索微生物群落协同降解木质纤维素的机理提供借鉴。     

Microbial degradation of alkenylbenzenes

Alkenylbenzenes are produced in large quantities by the petrochemical industry. The simplest of these alkenylbenzenes, styrene, is in widespread use in the polymer-processing industry and is thus found in many industrial effluents. Airborne gaseous emissions of styrene are particular problems due to the potential toxicity and carcinogenicity of the compound. The catabolic pathways involved in the degradation of styrene have been well characterised. With an increased knowledge of the adaptative response which microorganisms exhibit when exposed to higher styrene concentrations, together with an understanding of the genetic regulation of the catabolic pathways which operate in these microbial strains, it is likely that these organisms could be exploited in areas such as biotransformations, biocatalysis and bioremediation.The authors are with the Microbiology Department, University College, Cork, Ireland.