Enrichment of a microbial community performing anaerobic oxidation of methane in a continuous high-pressure bioreactor
© Zhang et al; licensee BioMed Central Ltd. 2011
Received: 16 December 2010
Accepted: 16 June 2011
Published: 16 June 2011
Anaerobic oxidation of methane coupled to sulphate reduction (SR-AOM) prevents more than 90% of the oceanic methane emission to the atmosphere. In a previous study, we demonstrated that the high methane pressure (1, 4.5, and 8 MPa) stimulated in vitro SR-AOM activity. However, the information on the effect of high-pressure on the microbial community structure and architecture was still lacking.
In this study we analysed the long-term enrichment (286 days) of this microbial community, which was mediating SR-AOM in a continuous high-pressure bioreactor. 99.7% of the total biovolume represented cells in the form of small aggregates (diameter less then 15 μm). An increase of the total biovolume was observed (2.5 times). After 286 days, the ANME-2 (anaerobic methanotrophic archaea subgroup 2) and SRB (sulphate reducing bacteria) increased with a factor 12.5 and 8.4, respectively.
This paper reports a net biomass growth of communities involved in SR-AOM, incubated at high-pressure.
Anaerobic oxidation of methane coupled to sulphate reduction (SR-AOM) is a major process determining deep-sea geochemistry and cold-seep ecosystems. First of all, it controls the atmospheric methane efflux from the ocean floor, consuming more than 90% of the methane produced in marine sediments . Moreover, it fuels the deep sea ecosystem by channelling thermal generated and biogenetic methane into organic matter and carbonate. Finally, SR-AOM shapes the sea floor landscape by contributing to bicarbonate and alkalinity production, resulting in massive carbonate precipitation . The overall SR-AOM reaction is:
Two groups of microorganisms are the key players in SR-AOM process: anaerobic methanotrophic archaea (ANME) with three groups (ANME-1, ANME-2 and ANME-3) and sulphate reducing bacteria (SRB) [3–6]. All ANME groups discovered so far are related clades of methanogens, while their SRB partner was always found in the same environment with or without forming spatial closely related consortia . However, neither ANME nor SRB from SR-AOM active spots has been obtained in pure culture yet. The main difficulty lies on the extremely long doubling time (several months) and low growth yield (0.05 g dry weight/g carbon oxidized) of ANME and SRB from in vitro incubations [8–10].
To stimulate the in vitro SR-AOM activity and to enrich the SR-AOM community, different types of bioreactors, which can be operated at ambient/high pressure in continuous/batch mode, have been developed by different research groups [10–14]. Due to the extremely low affinity for methane (Km of 37 mM) and the low methane solubility at ambient pressure, high-pressure bioreactors have the advantage of permitting a higher SR-AOM activity [11, 15]. Nevertheless, it is still unknown if the high-pressure bioreactor also confers advantage on biomass enrichment, and if it has an effect on selective enrichment of certain groups of ANME. Moreover, the information is lacking on the community architecture inside the high-pressure bioreactor, meaning if the microbes live as single cells or form consortia.
Through high-pressure incubation, we have obtained an enrichment originating from a Mud Volcano from the Gulf of Cadiz, performing anaerobic oxidation of methane. The SR-AOM activities at different incubation conditions have been described previously . In this study, the community structure and architecture of this enrichment were investigated. The potential growth of ANME and SRB under high pressure has been evaluated.
Results and Discussion
Community architectural distribution
Cell aggregates accounted for the major part of the biovolume (Figure 1B). The middle size aggregates (Ø = 6, 7, 8, 9, 10 μm) contributed for about half of the total biovolume (52.73 ± 9.04% in S1 and 47.02 ± 8.67% in S2). Although the big size aggregates (Ø = 11, 12, 13, 14, 15 μm) had very low concentrations (2.22 ± 0.74 *105/ml slurry in S1 and 4.93 ± 1.56 *105/ml slurry as shown in Figure 1A), they also contributed for large part of the biovolume (26.67 ± 7.83% in S1 and 33.34 ± 8.54% in S2).
Enrichment of total biomass
The total biovolume concentration increased from (1.28 ± 0.06)*109 μm3/ml slurry in S1 to (4.49 ± 0.51)*109 μm3/ml slurry in S2 (Figure 1B). Since the reactor volume was fixed and the biomass washing out during reactor operation was negligible , the total biomass inside the reactor increased 2.5 times within 286 days. This reactor system was the first system that was able to accumulate total biomass while maintaining high SR-AOM activity--0.5 mmol sulfide production per day while the reactor was operated at batch mode under 8 MPa methane pressure . In the systems previously reported by other authors, either only specific groups but not the total biomass was quantified  or there was major loss of biomass due to sampling and decay [9, 10].
The biovolume data was converted into cell dry weight for a comparison with VSS (Volatile Suspended Solids) data. Taken the same assumption as described by Nauhaus et al. , there was about 0.2 g cell dry weight/ml biovolume in the sediment sample with SR-AOM activity. Therefore the biomass concentration in the high-pressure bioreactor increased from 0.3 (g cell dry weight/l slurry) in S1 to 0.9 (g cell dry weight/l slurry) in S2. However, this value was one order lower compared to the 8 g/l of VSS (based on weight difference between drying sample at 105°C and at 650°C) as reported by Zhang et al. . One possibility is that the assumption 0.2 g cell dry weight/ml biovolume was based on analysis of two strains of small marine microorganism [9, 17], which could be not representative of the cells enriched in the reactor. Another possibility would be the extracellular polymeric substances (EPS) contributed large part of VSS. For example, for granular microbial aggregates enriched in an OLAND (oxygen-limited autotrophic nitrification-denitrification) reactor, as much as 50-80% of the space occupied by bacteria was constituted of EPS . For the deep-sea sediment, the presence of EPS has been reported both from in situ sediment and in vitro enrichments at different locations [9, 19]. However whether the production of EPS was stimulated during high-pressure incubations and what was the mechanism behind still needs to be further investigated.
Primers and probes used in this study.
Sequence (5' to 3')
TTC CGG TTG ATC CYG CCG GA
YCC GGC GTT GAM TCC AAT T
AGA GTT TGA TCC TGG CTC AG
GGT TAC CTT GTT ACG ACT T
AGT TTT CGC GCC TGA TGC
AGC TCC ACC CGT TGT AGT
TCG GAG TAG GGA CCC ATT
GTC CCA ATC ATT GTA GCC GGC
Helper probe for ANME3-1249
TTA TGA GAT TAC CAT CTC CTT
Helper probe for ANME3-1249
TCC ACT TCC CTC TCC CAT
Desulfosarcina spp., Desulfofaba spp., Desulfococcus spp., Desulfofrigus spp.
Community composition based on CARD-FISH analysis
% of cell count 1
% of aggregate count 1
% of biovolume1
Below detection limit2
Below detection limit2
Below detection limit2
8.2 ± 3.0
37.1 ± 6.2
13.4 ± 4.2
0.1 ± 0.1
2.1 ± 1.4
1.5 ± 1.5
2.9 ± 1.5
32.0 ± 6.2
22.7 ± 5.3
Below detection limit3
Below detection limit3
Below detection limit3
2.5 ± 2.0
47.2 ± 8.2
50.4 ± 15.9
0.1 ± 0.1
0.8 ± 0.7
2.4 ± 1.8
0.8 ± 0.4
37.6 ± 5.0
60.6 ± 5.5
Enrichment of ANME-2 and SRB
CARD-FISH results showed that percentages of ANME-2 and SRB biovolume increased from 13.4 ± 4.2% and 22.7 ± 5.3% in S1 to 50.4 ± 15.9% and 60.6 ± 5.5% in S2 (Table 2). By combining with the total biovolume data from DAPI staining (Figure 1B), the biovolume of ANME-2 in S1 was:
(1.28*109 μm3/ml slurry) * 13.4% = 1.7*108 μm3/ml slurry
The biovolume of ANME-2 in S2 was:
(4.49*109 μm3/ml slurry) * 50.4% = 2.3*109 μm3/ml slurry
Therefore after 286 days incubation, the ANME-2 population increased for 12.5 times. Following the same method of calculation, the SRB population increased for 8.4 times after 286 days incubation in this high-pressure bioreactor. The populations of ANME-2 and SRB both increased faster than the total biomass, which indicated that ANME-2 and SRB were selectively enriched in the system. This selective enrichment of ANME-2 and SRB was another proof that the incubation condition inside this high-pressure bioreactor was favourable for SR-AOM community.
Comparison of doubling times of ANME in different enrichment systems
Doubling time (months)
Gulf of Mexico
ANME-2a/2c and SRB consortia
After 286 days incubation in a simulated cold seep environment under high methane pressure, ANME-2 and SRB in the sediment from Captain Arutyunov Mud Volcano were enriched. Based on biovolume calculation, the populations of ANME-2 and SRB increased for 12.5 times and 8.4 times. Within total biomass volume, 99.7% was accounted from aggregates. Therefore the incubation condition apparently favoured the cells to form aggregates, especially in small size (2<Ø≤5 μm), rather than to live as single cells. No aggregate bigger than 15 μm in diameter was observed; they apparently divided after reaching a critical size. Based on the 16S rRNA gene clone library, the archaeal diversity was low, and contained only ANME-2 (88%) and MBG-D (12%). In contrast, the bacterial community was highly diverse.
In a previous study, the sediment sample originally from Captain Arutyunov Mud Volcano (Gulf of Cadiz, North East Atlantic) was diluted 12 times with artificial sea water medium and incubated in a continuous high-pressure bioreactor at 15°C . This bioreactor system was a simulator for cold seep ecosystems, where sulphate and high-pressure methane were supplied. Because the high apparent affinity for methane (37 mM) in SR-AOM reaction and low dissolubility of methane in seawater (1.3 mM at 15°C at ambient pressure), it is necessary to supply high pressure methane to obtain high concentration of dissolved methane which can be directly used by microorganisms for high in vitro SR-AOM activity . During this research, the reactor was operated in a fed-batch mode or a continuous mode. When it was in fed-batch mode, the methane pressures were switched between 1, 4.5 and 8 MPa. When it was in continuous mode, the methane pressure was either 1 or 8 MPa and the flow rate was 0.1 ml/min (HRT 100 hours). The SR-AOM activities under different operational conditions have been described previously . To take a slurry sample, the incubation vessel was open under a nitrogen atmosphere and manually stirred to make the slurry sample homogeneous. The slurry samples before (S1) and after (S2) 286 days incubation were fixed in 4% formaldehyde and stored at 4°C for cell staining. Additional slurry from S2 was stored at -20°C for DNA extraction and clone library analysis.
Cell and aggregates quantification
To assess the number and the size of cells and aggregates, DAPI (4', 6-diamidino-2-phenylindole) staining was performed on S1 (after 2000 times dilution) and S2 (after 5600 times dilution). Subsequently, the samples were filtrated onto a circular GTTP polycarbonate filter (0.2 μm, Millipore, Germany) with a diameter of 2.5 cm. The number of cells (or aggregates) was quantified under a microscope (Zeiss, Carl Zeiss Microimaging GmbH, Germany) at 1,000 times magnification. The diameter of a single cell was assumed as 0.45 μm, which is the average size of ANME and SRB cells [3, 9]. The diameters of the aggregates were measured according to a reference scale bar built in the eyepiece of the microscope. The biovolume was calculated assuming that both cells and aggregates have spherical shapes. For each sample, 4 individual staining were applied. For each staining 50 fields of view were counted for calculation.
Cell and aggregates identification
In order to evaluate which type of ANME and SRB were present and enriched in the reactor, catalyzed reporter deposition fluorescence in situ hybridization (CARD-FISH) was applied on S1 and S2. The slurry samples were embedded onto GTTP filters. The filters were incubated in methanol with 0.15% H2O2 for 30 min at room temperature before washed with water and ethanol and dried. For each sample, 2 filters were prepared. One was incubated in lysozyme solution (10 mg/ml in 0.05 M EDTA, pH 8.0; 0.1 M Tris-HCl, pH 8.0) for 15 min at 37°C to achieve permeablilization of bacterial cells, and another one was incubated in Proteinase K solution (15 μg/ml in MilliQ water) for 3 min at room temperature to achieve permeabilization of achaeal cells. Afterwards the filters were cut into 4 pieces. Each piece was for hybridization with one probe (Table 1). The hybridization was performed according to the protocol previously described . After hybridization, the filter was stained with DAPI to target all cells present on the filter.
During CARD-FISH, a few steps of washing the filter may cause the loss of cells and aggregates. It was assumed that all types of cells or aggregates were washed out in the same ratio. Therefore the percentage of ANME or SRB among the total cells did not change after washing. For each hybridization, cells and aggregates in 50 fields of view were analyzed under microscope. For each field, both probe staining and DAPI staining were counted to quantify the concentration of ANME-1 (or ANME-2, ANME-3 and SRB) among total biomass.
For a more detailed investigation on the microbial community, the archaeal and bacterial 16S rRNA gene clone libraries were performed on S2 according to protocol previously described [24, 25] with the primers listed in Table 1. For archaeal library, 56 clones were obtained while 50 clones were randomly picked for sequencing. For bacterial library, 110 clones were obtained while 100 clones were picked for sequencing. The sequences were compared with their best match in NCBI to classify their phylogenetic group (Additional file 1, Table S1). To calculate the percentage of each phylogenetic group into total archaeal/bacterial community, the number of clones within one phylogenetic group was divided by the number of sequenced clones within archaeal/bacterial library. All the sequences described in the paper have been deposited in the databases of GenBank, under accession numbers HQ405602 to HQ405741. The archaeal hpylogenetic tree has been constructed by Maximum Likelihood based on 212 sequences using the online RaxML tool at http://phylobench.vital-it.ch/raxml-bb/index.php. The bacterial phylogenetic tree has been constructed using the online maximum likelihood tool at http://www.atgc-montpellier.fr/phyml/.
This work was supported by a PhD grant from the Bijzonder Onderzoeks Fonds of Ghent University (BOF08/DOC/016, BOF09/GOA/005), a research fund from the National High-Tech Program of China (2007AA091904), a research fund from the China State Key Laboratory of Ocean Engineering (AE010802) and a research fund from the European Science Foundation MicroSYSTEMS supported by Fonds voor Wetenschappelijk Onderzoek (506G.0656.05). We thank Siegfried E. Vlaeminck and Beatriz Guimarães for their critical review on this manuscript.
- Reeburgh WS: Oceanic methane biogeochemistry. Chem Rev. 2007, 107 (2): 486-513. 10.1021/cr050362v.PubMedView ArticleGoogle Scholar
- Stadnitskaia A, Muyzer G, Abbas B, Coolen MJL, Hopmans EC, Baas M, van Weering TCE, Ivanov MK, Poludetkina E, Damste JSS: Biomarker and 16S rDNA evidence for anaerobic oxidation of methane and related carbonate precipitation in deep-sea mud volcanoes of the Sorokin Trough, Black Sea. Marine Geology. 2005, 217 (1-2): 67-96. 10.1016/j.margeo.2005.02.023.View ArticleGoogle Scholar
- Knittel K, Losekann T, Boetius A, Kort R, Amann R: Diversity and distribution of methanotrophic archaea at cold seeps. Applied and Environmental Microbiology. 2005, 71 (1): 467-479. 10.1128/AEM.71.1.467-479.2005.PubMedPubMed CentralView ArticleGoogle Scholar
- Boetius A, Ravenschlag K, Schubert CJ, Rickert D, Widdel F, Gieseke A, Amann R, Jorgensen BB, Witte U, Pfannkuche O: A marine microbial consortium apparently mediating anaerobic oxidation of methane. Nature. 2000, 407 (6804): 623-626. 10.1038/35036572.PubMedView ArticleGoogle Scholar
- Hinrichs KU, Hayes JM, Sylva SP, Brewer PG, DeLong EF: Methane-consuming archaebacteria in marine sediments. Nature. 1999, 398 (6730): 802-805. 10.1038/19751.PubMedView ArticleGoogle Scholar
- Orphan VJ, Hinrichs KU, Ussler W, Paull CK, Taylor LT, Sylva SP, Hayes JM, Delong EF: Comparative analysis of methane-oxidizing archaea and sulfate-reducing bacteria in anoxic marine sediments. Applied and Environmental Microbiology. 2001, 67 (4): 1922-1934. 10.1128/AEM.67.4.1922-1934.2001.PubMedPubMed CentralView ArticleGoogle Scholar
- Knittel K, Boetius A: Anaerobic Oxidation of Methane: Progress with an Unknown Process. Annual Review of Microbiology. 2009, 63: 311-334. 10.1146/annurev.micro.61.080706.093130.PubMedView ArticleGoogle Scholar
- Thauer RK, Shima S: Methane as fuel for anaerobic microorganisms. Incredible Anaerobes: From Physiology to Genomics to Fuels. Edited by: Wiegel J, Maier RJ, Adams MWW. 2008, Oxford: Blackwell Publishing, 1125: 158-170. 10.1196/annals.1419.000.Google Scholar
- Nauhaus K, Albrecht M, Elvert M, Boetius A, Widdel F: In vitro cell growth of marine archaeal-bacterial consortia during anaerobic oxidation of methane with sulfate. Environmental Microbiology. 2007, 9 (1): 187-196. 10.1111/j.1462-2920.2006.01127.x.PubMedView ArticleGoogle Scholar
- Meulepas RJW, Jagersma CG, Gieteling J, Buisman CJN, Stams AJM, Lens PNL: Enrichment of Anaerobic Methanotrophs in Sulfate-Reducing Membrane Bioreactors. Biotechnol Bioeng. 2009, 104 (3): 458-470. 10.1002/bit.22412.PubMedView ArticleGoogle Scholar
- Zhang Y, Henriet J-P, Bursens J, Boon N: Stimulation of in vitro anaerobic oxidation of methane rate in a continuous high-pressure bioreactor. Bioresource Technology. 2010, 101 (9): 3132-3138. 10.1016/j.biortech.2009.11.103.PubMedView ArticleGoogle Scholar
- Girguis PR, Orphan VJ, Hallam SJ, DeLong EF: Growth and Methane Oxidation Rates of Anaerobic Methanotrophic Archaea in a Continuous-Flow Bioreactor. Applied and Environmental Microbiology. 2003, 69 (9): 5472-5482. 10.1128/AEM.69.9.5472-5482.2003.PubMedPubMed CentralView ArticleGoogle Scholar
- Nauhaus K, Boetius A, Kruger M, Widdel F: In vitro demonstration of anaerobic oxidation of methane coupled to sulphate reduction in sediment from a marine gas hydrate area. Environ Microbiol. 2002, 4 (5): 296-305. 10.1046/j.1462-2920.2002.00299.x.PubMedView ArticleGoogle Scholar
- Deusner C, Meyer V, Ferdelman TG: High-Pressure Systems for Gas-Phase Free Continuous Incubation of Enriched Marine Microbial Communities Performing Anaerobic Oxidation of Methane. Biotechnol Bioeng. 2009, 105 (3): 524-533. 10.1002/bit.22553.View ArticleGoogle Scholar
- Yamamoto S, Alcauskas JB, Crozier TE: Solubility of methane in distilled water and seawater. J Chem Eng Data. 1976, 21 (1): 78-80. 10.1021/je60068a029.View ArticleGoogle Scholar
- Girguis PR, Cozen AE, DeLong EF: Growth and population dynamics of anaerobic methane-oxidizing archaea and sulfate-reducing bacteria in a continuous-flow bioreactor. Appl Environ Microbiol. 2005, 71 (7): 3725-3733. 10.1128/AEM.71.7.3725-3733.2005.PubMedPubMed CentralView ArticleGoogle Scholar
- Robertson BR, Button DK, Koch AL: Determination of the biomasses of small bacteria at low concentrations in a mixture of species with forward light scatter measurements by flow cytometry. Applied and Environmental Microbiology. 1998, 64 (10): 3900-3909.PubMedPubMed CentralGoogle Scholar
- Vlaeminck SE, Terada A, Smets BF, De Clippeleir H, Schaubroeck T, Bolca S, Demeestere L, Mast J, Boon N, Carballa M, et al: Aggregate Size and Architecture Determine Microbial Activity Balance for One-Stage Partial Nitritation and Anammox. Applied and Environmental Microbiology. 2010, 76 (3): 900-909. 10.1128/AEM.02337-09.PubMedPubMed CentralView ArticleGoogle Scholar
- Jagersma GC, Meulepas RJW, Heikamp-de Jong I, Gieteling J, Klimiuk A, Schouten S, Damste JSS, Lens PNL, Stams AJM: Microbial diversity and community structure of a highly active anaerobic methane-oxidizing sulfate-reducing enrichment. Environmental Microbiology. 2009, 11 (12): 3223-3232. 10.1111/j.1462-2920.2009.02036.x.PubMedView ArticleGoogle Scholar
- Schreiber L, Holler T, Knittel K, Meyerdierks A, Amann R: Identification of the dominant sulfate-reducing bacterial partner of anaerobic methanotrophs of the ANME-2 clade. Environmental Microbiology. 2010, 12 (8): 2327-2340. 10.1111/j.1462-2920.2010.02275.x.PubMedGoogle Scholar
- Lidstrom M: Aerobic Methylotrophic Prokaryotes. The Prokaryotes. Edited by: Dworkin M, Falkow S, Rosenberg E, Schleifer K-H, Stackebrandt E. 2006, New York: Springer, 2: 618-634.View ArticleGoogle Scholar
- Kruger M, Wolters H, Gehre M, Joye SB, Richnow H-H: Tracing the slow growth of anaerobic methane-oxidizing communities by (15)N-labelling techniques. FEMS Microbiol Ecol. 2008, 63 (3): 401-411. 10.1111/j.1574-6941.2007.00431.x.PubMedView ArticleGoogle Scholar
- Pernthaler A, Pernthaler J, Amann R: Fluorescence in situ hybridization and catalyzed reporter deposition for the identification of marine bacteria. Applied and Environmental Microbiology. 2002, 68 (6): 3094-3101. 10.1128/AEM.68.6.3094-3101.2002.PubMedPubMed CentralView ArticleGoogle Scholar
- Jiang LJ, Zheng YP, Peng XT, Zhou HY, Zhang CL, Xiao X, Wang FP: Vertical distribution and diversity of sulfate-reducing prokaryotes in the Pearl River estuarine sediments, Southern China. FEMS Microbiol Ecol. 2009, 70 (2): 249-262. 10.1111/j.1574-6941.2009.00758.x.View ArticleGoogle Scholar
- Wang SF, Xiao X, Jiang LJ, Peng XT, Zhou HY, Meng J, Wang FP: Diversity and Abundance of Ammonia-Oxidizing Archaea in Hydrothermal Vent Chimneys of the Juan de Fuca Ridge. Applied and Environmental Microbiology. 2009, 75 (12): 4216-4220. 10.1128/AEM.01761-08.PubMedPubMed CentralView ArticleGoogle Scholar
- Stamatakis A, Hoover P, Rougemont J: A Rapid Bootstrap Algorithm for the RAxML Web Servers. Syst Biol. 2008, 57 (5): 758-771. 10.1080/10635150802429642.PubMedView ArticleGoogle Scholar
- Guindon S, Gascuel O: A simple, fast, and accurate algorithm to estimate large phylogenies by maximum likelihood. Syst Biol. 2003, 52 (5): 696-704. 10.1080/10635150390235520.PubMedView ArticleGoogle Scholar
- Delong EF: Archaea in coastal marine environments. Proc Natl Acad Sci USA. 1992, 89 (12): 5685-5689. 10.1073/pnas.89.12.5685.PubMedPubMed CentralView ArticleGoogle Scholar
- Lane DJ: 16S/23S rRNA sequencing. Nucleic Acid Techniques in Bacterial Systematics. Edited by: Stackebrandt E. 1991, Goodfellow M: John Wiley & Sons, 142-175.Google Scholar
- Reysenbach AL, Wickham GS, Pace NR: Phylogenetic analysis of the hyperthermophilic pink filament community in Octopus Spring, Yellowstone National Park. Appl Environ Microbiol. 1994, 60 (6): 2113-2119.PubMedPubMed CentralGoogle Scholar
- Niemann H, Losekann T, de Beer D, Elvert M, Nadalig T, Knittel K, Amann R, Sauter EJ, Schluter M, Klages M, et al: Novel microbial communities of the Haakon Mosby mud volcano and their role as a methane sink. Nature. 2006, 443 (7113): 854-858. 10.1038/nature05227.PubMedView ArticleGoogle Scholar
- Losekann T, Knittel K, Nadalig T, Fuchs B, Niemann H, Boetius A, Amann R: Diversity and abundance of aerobic and anaerobic methane oxidizers at the Haakon Mosby mud volcano, Barents Sea. Appl Environ Microbiol. 2007, 73 (10): 3348-3362. 10.1128/AEM.00016-07.PubMedPubMed CentralView ArticleGoogle Scholar
- Manz W, Eisenbrecher M, Neu TR, Szewzyk U: Abundance and spatial organization of Gram-negative sulfate-reducing bacteria in activated sludge investigated by in situ probing with specific 16S rRNA targeted oligonucleotides. FEMS Microbiol Ecol. 1998, 25 (1): 43-61. 10.1111/j.1574-6941.1998.tb00459.x.View ArticleGoogle Scholar
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