Halogenated compounds constitute one of the largest groups of environmental
pollutants, partly as a result of their widespread use as biocides, solven
ts and other industrial chemicals. A critical step in degradation of organo
halides is the cleavage of the carbon-halogen bond. Reductive dehalogenatio
n is generally the initial step in metabolism under methanogenic conditions
, which requires a source of reducing equivalents, with the halogenated com
pound serving as an electron acceptor. Dehalogenation is greatly influenced
by alternate electron accepters; e.g. sulfate frequently inhibits reductiv
e dehalogenation. On the other hand, a number of halogenated aromatic compo
unds can be degraded under different electron-accepting conditions and thei
r complete oxidation to CO2 can be coupled to processes such as denitrifica
tion, iron(III)-reduction, sulfate reduction and methanogenesis. Reductive
dehalogenation was the initial step in degradation not only under methanoge
nic, but also under sulfate-and iron(III)-reducing conditions. Dehalogenati
on rates were in general slower under sulfidogenic and iron-reducing condit
ions, suggesting that dehalogenation was affected by the electron acceptor.
The capacity for dehalogenation appears to be widely distributed in anoxic
environments; however, the different substrate specificities and activitie
s observed for the halogenated aromatic compounds suggest that distinct deh
alogenating microbial populations are enriched under the different reducing
conditions. Characterization of the microbial community structure using a
combination of biomolecular techniques, such as cellular fatty acid profili
ng, and 16 S rRNA fingerprinting/sequence analysis, was used to discern the
distinct populations enriched with each substrate and under each electron-
accepting condition. These combined techniques will aid in identifying the
organisms responsible for dehalogenation and degradation of halogenated aro
matic compounds. (C) 2000 Elsevier Science Ltd. All rights reserved.