INTRODUCTION

Top Abstract Introduction Materials and Methods Results Discussion References

Methanotrophic bacteria are a physiologically unique group of microorganisms distinguished by their ability to use methane as sole source of carbon and energy (for a review, see reference 24). Microbial ecologists have long been interested in the methanotrophs due to their key role in the global methane cycle, oxidizing CH₄ to CO₂ (33). The first step in this process is catalyzed by the enzyme methane monooxygenase, of which two forms are known: the particulate methane monooxygenase, a membrane-bound enzyme present in all methanotrophs examined to date (50), and the soluble methane monooxygenase (sMMO), a cytoplasmic enzyme present in only select species (37). Both forms fortuitously oxidize a number of compounds, like the common environmental contaminant trichloroethylene (15, 56). Accordingly, this group of bacteria has attracted interest in regard to their potential for bioremediation (17, 26).

Landfills produce large amounts of CH₄ due to methanogenic activity under anaerobic conditions (32). However, very high rates of CH₄ oxidation and large methanotrophic populations have been reported in the oxic portion of landfill cover soils (30, 60). CH₄ is a potent greenhouse gas, and methanotrophs play an important role in reducing the amount of CH₄ released into the atmosphere (54). Thus, understanding the community structure of methanotrophic bacteria in landfill soil may help one better manage the attenuation of CH₄ emission by these microorganisms.

One of the most fundamental discoveries made by microbiologists during the last decade has been the realization that the vast majority of bacteria in the environment have not yet been cultured (1). Using molecular biological tools and employing the 16S rRNA gene as a marker, microbiologists have been able to identify the presence of novel, uncultured organisms in situ. These 16S rRNA-based approaches have led to estimates of prokaryotic biodiversity and surveys of the microbial community structure of many environments (3, 9, 36, 57, 59, 61). At present, one of the most burning questions is the relationship between the microbial communities as described by these culture-independent methods and community structure assessment based on culturing. Investigators exploring the wide range of microbial diversity with universal- or domain-specific 16S rRNA probes or primers have only rarely reported the isolation of novel organisms whose presence was suggested by sequence analysis (29, 31, 46, 53). Often the reason is that genetic and metabolic traits cannot be predicted by the phylogenetic position of a clone sequence. Thus, the development of specific enrichment media remains troublesome.

For some bacterial groups, however, phylogenetic placement has been shown to be a reliable indicator of physiology. Traditionally, methane-oxidizing bacteria have been classified into three groups, based primarily on their biochemistry and morphological features (25). The type I methanotrophs employ the ribulose monophosphate pathway for formaldehyde assimilation and have disc-shaped bundles of intracytoplasmic membranes. The type II methanotrophs also assimilate carbon at the oxidation level of formaldehyde but use the serine pathway and show paired membrane structures at the periphery of the cell. The type X methanotrophs have disc-shaped bundles of intracytoplasmic membranes, use the ribulose monophosphate pathway (although they show a low level of activity for some of the enzymes in the serine cycle), and have a functional Calvin cycle. 16S ribosomal DNA (rDNA) sequence analysis has confirmed these three groupings. The type I methanotrophs form a phylogenetically coherent cluster within the gamma subdivision of the Proteobacteria (gamma-Proteobacteria), as do the type II methanotrophs within the alpha-Proteobacteria (8, 10). The type X species also fall within the gamma-Proteobacteria, but in a grouping distinct from type I. Recently, methanotroph taxonomy has been revised by a polyphasic approach, and the type I and type X methanotrophs have been included together in the family Methylococcaceae (6, 7). With one notable exception (14), it seems that within the alpha- and gamma-Proteobacteria no group of methanotrophs has any close relatives that are not methane utilizers (28).

We exploited the restricted phylogeny of the obligate methane oxidizers to design degenerate methanotroph-specific 16S rRNA PCR primers and used them to construct two clone libraries from DNA extracted directly from landfill soil, in an effort to describe the methanotrophic community structure in a culture-independent manner. Simultaneously, a culture-based diversity assessment was undertaken by using a serial dilution enrichment culture technique (11, 49) to isolate numerically dominant but potentially slow-growing species. Recently, novel methanotrophs have been isolated by employing medium of very low ionic strength and low pH (13, 14). Also, there is indication that the amount of CH₄ available influences competition between the type I and type II methanotrophs (2, 22). Type I methanotrophs outcompete type II species under conditions of low CH₄ and high O₂, whereas type II species tend to dominate under the inverse conditions. These factors were varied in our enrichment scheme in an effort to isolate as wide a range of methanotrophs as possible.

	MATERIALS AND METHODS

Top Abstract Introduction Materials and Methods Results Discussion References

16S rDNA primer design and testing. New degenerate type I and type II methanotroph primers were designed to amplify part of the 16S rRNA genes of all validly published methanotrophic bacteria sequenced to date. Potential primers were identified by aligning representative 16S rDNA sequences from all major radiations of the domain Bacteria to the type I and type II methanotroph sequences by using the PILE_UP program that is part of the University of Wisconsin's Genetics Computer Group (GCG) sequence analysis software package. Selected regions unique to each group were identified by using GCG's BOX_SHADE program, and these were tested against the GenBank, EMBL, and DDJB databases to check specificity. Putative probes were then analyzed for hairpin structures and the potential for probe duplex formation by using the OLIGO program (National Biosciences). The putative methanotroph-specific primers that emerged from these tests are listed in Table 1.

Sampling and soil characteristics. A soil sample was collected from the upper 10-cm soil layer at the Athens-Clarke County Municipal Landfill, Athens, Georgia, on 5 August 1998. The sampling area was a former refuse disposal area that accepted solid waste from 1987 to 1996 and was covered with approximately 2 feet of surrounding soil in 1996 (47a). Visible inspection revealed the soil sample to be mostly red clay. The soil was analyzed for carbon, hydrogen, and nitrogen content by the University of Georgia chemical analysis lab by using a carbon-hydrogen-nitrogen analyzer (Perkin-Elmer 240C elemental analyzer) and for copper content by using an inductively coupled plasma-mass spectrometer. The sample was found to contain 0.48% N, 3.93% C, and 1.80% H by weight, and the copper content of the soil was 139.22 ppm. The soil pH was 4.93, as determined by adding an equal volume of deionized, distilled water to the soil and measuring with a combination pH probe.

DNA extraction. DNA was extracted and purified directly from the landfill soil by using the FastDNA SPIN Kit for Soil (Bio101). The procedure was slightly modified from that given by the manufacturer in the following areas. To exclude any extracellular DNA present in the sample (55), 25 ml of sterile sodium phosphate buffer (120 mM, pH 7.6) was added to 10 g of soil and the mixture was placed on a shaker table for 10 min at 150 rpm. The slurry was centrifuged at 6,000 × g for 10 min. One-half gram of the washed soil was added to the MULTIMIX2 tissue matrix tube, and 978 µl of the sodium phosphate buffer and 122 µl of the MT buffer were added. The tube was then secured in a mini-beadbeater (Biospec Products) and processed for two 1-min intervals with an intervening minute on ice. The MULTIMIX2 tubes were centrifuged at 14,000 × g for 30 s, 250 µl of the PPS reagent was added to the supernatant, and the tube was inverted by hand 10 times. Precipitate was pelleted at 14,000 × g for 5 min and divided into two tubes to which 0.5 ml of binding matrix suspension was added. The tubes were placed on a rotator for 2 min and then placed in a rack for 3 min to facilitate settling of the matrix. Approximately 250 µl of the supernatant was discarded from each tube, and the remaining binding matrix was pooled, transferred to a SPIN filter, and centrifuged at 14,000 × g for 1 min. Five hundred microliters of SEWS-M was added to the SPIN filter and centrifuged at 14,000 × g for 1 min. The remaining matrix was then dried by centrifuging at 14,000 × g for 2 min and allowed to air dry for 5 min. DNA was eluted from the binding matrix with 100 µl of double-distilled H₂O. The resultant DNA was quantified by using a fluorometer with Hoescht dye 33258 (34). The final yield was approximately 9.5 µg of DNA/g (wet weight) of soil.

PCR and construction of clone libraries. Purified environmental DNA was amplified by PCR by using Ready-to-Go PCR beads (Pharmacia) according to the manufacturer's instructions. To amplify type I 16S rDNA sequences present in the environmental DNA, the primers MethT1bR and MethT1dF (Table 1) were used at a final concentration of 0.4 µM each, along with approximately 100 ng of environmental DNA as the template. Type II sequences were amplified with primer MethT2R (Table 1) and the Bacteria-specific primer 27F (5'-GAGTTTGATCMTGGCTCAG-3') (35), both at a final concentration of 0.4 µM and with approximately 100 ng of the environmental DNA. The specifics of the PCR were as described above in the primer testing section. PCR products were visualized on an agarose gel, the correct size was confirmed, and the bands were excised and purified by using the Prep-a-Gene (Bio-Rad) gel purification protocol. To construct the type I and type II clone libraries, the purified PCR products were cloned into pCR2.1 by using the original TA cloning kit (Invitrogen) following the procedure recommended by the manufacturer.

Enrichment conditions and strain isolation. An extinction-dilution technique was used to isolate the numerically dominant methanotrophs from the landfill soil (11, 49). Seven dilution series were performed with combinations of three variables. First, the initial pH of the medium was adjusted with concentrated phosphoric acid to 4.8 (from the standard 6.8) for some enrichment series. Second, the enrichments were performed under different air/CH₄/CO₂ headspace ratios (50:45:5 versus 90:9:1). Lastly, the concentration of the nitrate minimal salts (NMS) medium (25) was diluted fivefold (1× NMS medium versus 0.2× NMS medium). The specific conditions of each enrichment series and its letter designation used for the isolate names are given in Table 2. For each series, 0.2 g (wet weight) of landfill soil was added to 1.8 ml of medium and the tube was vortexed vigorously for 3 min before the mixture was serially diluted to a final dilution of 10¹⁰. After 8 days of incubation at 30°C with moderate shaking at 150 rpm, the highest dilution displaying visual turbidity was plated on the same medium solidified with highly purified agar (Becton Dickinson). Colonies from plates were repeatedly picked and streaked on the same medium and incubated under the same conditions in an effort to achieve purity. Culture purity was determined by incubating putative methanotroph isolates with and without methane, checking for growth on nutrient agar, and phase-contrast microscopy. Despite repeated streaking, we were unable to obtain some type II methanotrophs in pure culture. When such cultures were examined microscopically, small cells with morphological features typical of Hyphomicrobium spp. were observed. Hyphomicrobia and similar bacteria are known to copurify with methanotrophs; they likely utilize methanol or other organic waste products that the methanotrophs excrete (23, 25). This was not always an obligate association, however. Many type II methanotrophs, including the novel type II isolates AML-A3 and AML-A6, could be purified with repeated streaking. We were still able to screen methanotrophs not in pure culture by exploiting the specificity of the type I and type II primer pairs described above on DNA isolated from the mixed methanotrophic cultures.

Partial sequencing and phylogenetic analysis. Ten plasmids with the full-length clone insert (approximately 920 bp for the type I library and 950 bp for the type II library) were sequenced from the type I and type II libraries with primers T1dF and 27F, respectively. Sequencing was done with an automated sequencer (model 373A; Applied Biosystems) at the Molecular Genetics Instrument Facility at the University of Georgia. Sequences were corrected by hand and compared to similar DNA sequences retrieved from the GenBank and EMBL databases by using the FASTA program, which is part of the GCG sequence analysis software package. For the isolates, partial 16S rDNA fragments were amplified with the methanotroph-specific primers described above and the PCR products were sequenced directly. Ten type I and 10 type II isolates of varying colony morphology from different enrichment dilution series were chosen for sequencing. Similar sequences were aligned by using the PILE_UP program of the GCG package. Phylogenetic trees were constructed by using the fastDNAml program (19, 47) run remotely via the World Wide Web at the Pasteur Institute (29a). Bootstrap analyses for 100 resamplings were performed to provide confidence estimates for tree topologies (18).

Sequencing and phylogenetic analysis of the full-length 16S rDNA and partial pmoA genes of selected isolates. Almost the entire 16S rRNA genes of isolates AML-C10, AML-D4, AML-A3, and AML-A6 were amplified with primers 27F and 1529R (5'-CAKAAAGGAGGTGATCC-3') (52) under the same conditions as described above, and both strands were sequenced with primers mentioned above (MethT1dF for type I isolates and 27F for type II isolates), in combination with 16S rDNA sequencing primers: 519R, 1392R, 357F, and 926F (35). Phylogenetic trees were constructed in the same manner as described above. Part of the pmoA gene from type II isolates AML-A3 and AML-A6 was amplified with the pmoA-specific primers pmoA189 (5'-GGNGACTGGGACTTCTGG-3') and pmoA682 (5'-GAASGCNGAGAAGAASGC-3') (27). Type I isolates AML-C10 and AML-D4 were used with primers pmof1 (5'-GGGGGAACTTCTGGGGITGGAC-3') and pmor (5'-GGGGGRCIACGTCITTACCGAA-3') to amplify a slightly smaller section of the pmoA gene (12). The PCR conditions for both sets of primers were the same as those described above. Both strands of the PCR products were sequenced directly with the pmoA-specific PCR primers mentioned above. Phylogenetic analysis of translated gene sequences was performed by using the PROTDIST (20) and neighbor-joining (48) applications that are part of the PHYLIP suite of phylogenetic analysis programs. Bootstrap analyses for 100 resamplings were performed to provide confidence estimates for tree topologies (18).

DGGE. A nested-PCR approach was used to profile the type I and type II methanotrophic communities by denaturing gradient gel electrophoresis (DGGE). The same amplification products used to construct the clone libraries were used as templates for PCR with the primers GC358F (5'-CGCCCGCCGCGCCCCGCGCCCGGCCCGCCGCCCCCGCCCCCCTACGGGAGGCAGCAG-3') and 517R (5'-ATTACCGCGGCTGCTGG-3'), which span variable region 3 (V3 region) of the 16S rRNA gene (44). Primer GC358F has a 40-bp GC clamp added to its 5' end. Hot-start and touchdown PCRs (16) were done to reduce primer-dimer complexes. The hot-start PCR procedure was as described above; the thermocycling program for touchdown PCR was as follows: initial denaturation was done at 94°C for 2 min 30 s and then at 94°C for 40 s, followed by touchdown primer annealing from 72 to 55°C (the annealing temperature was decreased 1°C for each cycle for the first 17 cycles to touchdown at 55°C), followed by extension at 72°C for 1 min (for each of the 17 cycles). Then 10 cycles of 94°C for 40 s, 55°C for 1 min, and 72°C for 1 min 30 s were done. Then 10 more cycles were performed at 94°C for 40 s, 55°C for 1 min 15 s, and 72°C for 2 min. The final extension step was 72°C for 7 min 30 s. For the clones and isolates, PCR was done directly by employing the primers described above with either plasmid DNA or chromosomal DNA serving as the template, respectively. PCR products were analyzed on agarose gels to confirm the presence of a single amplicand of the expected size. DGGE gels were 6.5% polyacrylamide with a denaturant gradient from 20 to 70% (for type I sequences) and 30 to 60% (for type II sequences). One hundred percent of the denaturant is 7 M urea and 40% deionized formamide. Gels were run in 1× TAE buffer (40 mM Tris base, 20 mM sodium acetate, 1 mM EDTA) for 4 h at 200 V at 60°C and visualized by ethidium bromide staining.

Nucleotide sequence accession numbers. The 16S rRNA gene sequences of isolates AML-C10, AML-D4, AML-A3, and AML-A6 have been deposited into GenBank, EMBL, and DDBJ nucleotide sequence databases and assigned accession no. AF177296, AF177297, AF177298, and AF177299, respectively. The partial pmoA gene sequences of these four isolates have been given accession no. AF177325 to AF177328. The partial 16S rDNA sequences of the other unique isolates (AML-A13, AML-A14, AML-E12, AML-E13, and AML-F18) have been assigned accession no. AF177300 to AF177304. The clones have been assigned accession no. AF177305 to AF177324.

	RESULTS

Top Abstract Introduction Materials and Methods Results Discussion References

Methanotroph-specific primers. Computer analyses of previously published methanotroph-specific phylogenetic probes indicated that some nondegenerate probes were too specific and would not hybridize to all methane oxidizers of the family Methylococcaceae. For example, probe 1035-RuMP (10), designed to hybridize to the type I methanotrophs, will not detect members of the former type X species, the genus Methylococcus. Since M. capsulatus is an efficient trichloroethylene-degrading species (24), the detection of this group in environmental samples would be beneficial for assessing bioremediation potential. To alleviate this problem, 16S rDNA primers and probes with a broader specificity were designed and tested. According to database searches, no one probe specific for the entire family Methylococcaceae could be identified, as all oligonucleotides chosen showed complete identity to at least one non-methane-utilizing organism or unknown clone sequence (Table 1). However, one oligonucleotide was identified (MethT2R) that was highly specific for all characterized type II methanotrophs (Table 1).

View larger version (94K): [in this window] [in a new window]   FIG. 1.   Ethidium bromide-stained agarose gel (1.5% [wt/vol]) showing PCR amplification products obtained with methanotroph-specific primers. See the text for details on primer design and reaction conditions. Lanes 1 to 6 show results with the type I primer set, MethT1dF and MethT1bR. Lanes 7 to 10 show results with the type II primer set, 27F and MethT2R. Template DNAs are as follows: lane 1, Methylomicrobium album; lane 2, Methylomonas methanica; lane 3, Methylobacter luteus; lane 4, M. capsulatus; lane 5, P. putida; lane 6, E. coli; lane 7, Methylosinus trichosporium; lane 8, Methylocystis parvus; lane 9, A. tumefaciens; and lane 10, S. meliloti.

Type I clone library. Ten clones that resulted from the use of the type I-specific primer pair on directly extracted environmental DNA from the landfill soil were sequenced with MethT1dF as the primer. This resulted in a range of between 640 and 675 usable bases for each clone. Database searches invariably indicated that the most closely related sequence to each of the 10 clones was the 16S rRNA gene of Methylobacter sp. strain BB5.1 (51). Methylobacter sp. strain BB5.1 is a NaCl-requiring strain recently isolated from estuary sediment. However, the range of sequence identity of the landfill clones with this species was quite low, ranging from 96.1% (clone T1-13) to 94.4% (clone T1-06). To better understand the relationship of clone sequences to the characterized type I methanotrophs, the clones were used in a phylogenetic analysis. Figure 2 shows the results of the phylogenetic analysis of all type I landfill clones and their relationship to some of the characterized type I methanotrophs of the genera Methylococcus, Methylomonas, Methylomicrobium, and Methylobacter and the type strains of two recently described genera, Methylosphaera (5) and Methylocaldum (4). Also included on this tree are some methanotrophic isolates from the landfill soil discussed in detail below. All landfill clones formed a distinct cluster most closely related to members of the genus Methylobacter. However, the high bootstrap value separating the clone sequences from any of the other known methanotrophs suggests that the clones form a monophyletic group distinct from the genus Methylobacter.

View larger version (25K): [in this window] [in a new window]   FIG. 2.   Phylogenetic tree showing the relationship of landfill soil type I methanotroph 16S rDNA clone sequences and type I AML isolates to some characterized methanotrophs from the family Methylococcaceae. This tree was constructed by using the fastDNAml program (47), which uses a maximum likelihood algorithm (19). A total of 625 aligned bases corresponding to E. coli positions 141 to 766 were used in this analysis. E. coli served as the outgroup. The scale bar represents 0.10 substitutions per base position. The numbers at the nodes of the tree indicate bootstrap values (18) for each node out of 100 bootstrap resamplings (values below 50 are not shown).

Type II clone library. Ten clones were also sequenced from the type II clone library with the 16S rDNA sequencing primer 27F. This resulted in a range of between 638 and 683 usable bases for each clone. Database searches indicated that five clones (T2-01, T2-04, T2-09, T2-10, and T2-13) showed the highest percentages of identity to Methylocystis sp. strain M, an sMMO-containing isolate which can degrade high levels of trichloroethylene (42). The identity of these clones to Methylocystis sp. strain M was high, ranging from 97.9 to 99.1%. Three clones (T2-02, T2-03, and T2-06) were found to be most closely related to an uncharacterized methanotrophic isolate, strain IMV B-3060 (10). These sequence identities were lower, ranging from 95.1 to 96.3%. Clones T2-07 and T2-17 were 96.1% and 96% identical, respectively, to each of three species (Methylocystis sp. strain M, strain IMV B-3060, and Methylosinus sporium). Figure 3 shows the results of the phylogenetic analysis of the type II clone sequences as they relate to some of the validly published type II methanotrophs and some uncharacterized strains. Also included on this tree are some landfill isolates discussed in detail below. According to this analysis, clones T2-01, T2-10, T2-13, and T2-04 group with Methylocystis echinoides, although the bootstrap value supporting this cluster is less than 50. Clone T2-09 is most closely related to a group containing Methylocystis parvus and Methylocystis sp. strain M, although again this cluster is not supported by high bootstrap values. None of the remaining clones clustered closely with any other characterized type II methanotroph.

View larger version (23K): [in this window] [in a new window]   FIG. 3.   Phylogenetic tree showing the relationship of landfill soil type II methanotroph 16S rDNA clone sequences and type II AML isolates to some characterized type II methanotrophs. Also included are some partially characterized methane oxidizers, including a recently isolated acidophilic bacterium, strain K, that diverges from the type II methanotrophs (14). This tree was constructed by using the fastDNAml program (47), which uses a maximum likelihood algorithm (19). A total of 623 aligned bases corresponding to E. coli positions 54 to 731 were used in this analysis. A. tumefaciens served as the outgroup. The scale bar represents 0.05 substitution per base position. The numbers at the nodes of the tree indicate bootstrap values (18) for each node out of 100 bootstrap resamplings (values below 50 are not shown).

Methanotroph isolation via dilution to extinction. After an 8-day incubation period, the highest dilution that showed growth was the 10⁶ dilution for the H and D series (series letter designations are given in Table 2). The A and E series showed growth at the 10⁵ dilution. The highest dilution that showed growth for the F and G series was the 10⁴ dilution. After being plated on solidified media, several colonies were selected for further purification on the basis of differences in colony morphology. Overall, 64 methane-utilizing cultures were obtained and 36 were screened with the type I- and type II-specific primer sets. The results of the screening are shown in Table 2. Of the three conditions varied, the concentration of the medium was the most important factor in selection for methanotrophic-type affiliation. Type II strains dominated all enrichments in 0.2× NMS medium. Only type I methanotrophs were enriched in full-strength NMS medium. Just one enrichment dilution series, series F, resulted in the isolation of both type I and type II strains.

Novel type I isolates AML-C10 and AML-D4. Ten-day-old colonies of both AML-C10 and AML-D4 grown on NMS medium were circular and light brown to buff colored and had regular margins. In liquid culture, both strains tended to grow in a flocculent manner, and the flocculent particles settled rapidly when shaking was ceased. The particles resembled irregularly shaped, sarcina-like aggregates when examined by phase-contrast microscopy. Individual AML-C10 cells were motile and coccus to oval shaped and had a diameter of approximately 1 to 1.5 µm. Individual AML-D4 cells were pleiomorphic; they commonly exhibited a fusiform morphology but were also present as long rods and sometimes chains of ovoid cells. Cell length ranged from 1.5 to 6 µm with a diameter of approximately 1 µm. At 30°C, strains AML-C10 and AML-D4 had doubling times of approximately 3.5 and 6.5 h, respectively.

View larger version (16K): [in this window] [in a new window]   FIG. 4.   Phylogenetic analysis of partial amino acid sequences of the pmoA gene from selected type I and type II methanotrophs, novel isolates and environmental clones (41). This unrooted tree was constructed by using the neighbor-joining method (48) from a matrix of pairwise genetic distances as calculated by the PROTDIST program (20). A total of 110 aligned amino acid positions were used in this analysis. The scale bar represents 10% sequence divergence. Bootstrap analyses (18) for 100 resamplings were performed to provide confidence estimates for tree topologies (values below 50 are not shown).

Novel type II isolates AML-A3 and AML-A6. Since phylogenetic analysis based on a partial 16S rDNA sequence showed AML-A3 and AML-A6 clustering with clones T2-02, T2-03, and T2-06 in a group distinct from the well-described type II methanotrophs, they were chosen for further analysis. Both AML-A3 and AML-A6 formed circular, mucoid colonies on NMS medium that were pink and white pigmented, respectively. In liquid culture, both strains grew in an evenly dispersed manner. Both were nonmotile and exhibited a coccus-shaped morphology. The doubling time at 30°C was approximately 12.75 h for AML-A3 and 16.5 h for AML-A6.

DGGE. DGGE was employed here to provide genetic fingerprints that could serve as an overview of the diversity of the type I and type II methanotrophic communities in the landfill soil. Figure 5 shows the results of DGGE analysis with the primer pair GC358F-517R (the V3 region) on type I sequences amplified from the landfill environmental DNA and selected clones and isolates. The type I community profile consists of 12 unique bands (Fig. 5, lanes 1 and 10). Two diffuse bands (labeled A and B) that denatured at relatively low denaturant concentrations accounted for the majority of the amplification products. Ten other discernable bands (C through L) denatured at higher denaturant concentrations and were present in a lesser abundance.

View larger version (129K): [in this window] [in a new window]   FIG. 5.   Type I methanotroph DGGE analysis. Shown is an ethidium bromide-stained 6.5% polyacrylamide denaturing gradient gel (20 to 70%) showing separation patterns based on sequence difference of the V3 region (approximate E. coli positions 341 to 534) of the 16S rDNA. Lanes 1 and 10, the type I landfill methanotrophic community (250 ng and 1.5 µg, respectively); lane 2, clone T1-08; lane 3, clone T1-01; lane 4, clone T1-14; lane 5, clone T1-09; lane 6, clone T1-02; lane 7, clone T1-04; lane 8, isolate AML-C10; lane 9, isolate AML-D4. Bands A through L are explained in the text.

View larger version (112K): [in this window] [in a new window]   FIG. 6.   DGGE analysis of cloned DNA extracted from type I community bands A and B (Fig. 5). Shown is an ethidium bromide-stained 6.5% polyacrylamide denaturing gradient gel (20 to 70%) showing separation patterns based on sequence differences in the V3 region (approximate E. coli positions 341 to 534) of the 16S rDNA. See Results for experimental details. Lane 1, clone EB-A1; lane 2, clone EB-A2; lane 3, type I landfill methanotrophic community profile; lane 4, clone EB-B1; lane 5, clone EB-B2; lane 6, clone T1-08; lane 7, clone T1-09.

View larger version (101K): [in this window] [in a new window]   FIG. 7.   Type II methanotroph DGGE analysis. Shown is an ethidium bromide-stained 6.5% polyacrylamide denaturing gradient gel (30 to 60%) showing separation patterns based on sequence differences in the V3 region (approximate E. coli positions 341 to 534) of the 16S rDNA. Lanes 1 and 10, the type II landfill methanotrophic community; lane 2, clone T2-06; lane 3, clone T2-07; lane 4, clone T2-03; lane 5, clone T2-02; lane 6, clone T2-01; lane 7, isolate AML-A3; lane 8, isolate AML-F18; lane 9, isolate AML-E13. Bands A through I are explained in the text.

	DISCUSSION

Top Abstract Introduction Materials and Methods Results Discussion References

In this report we describe the isolation of new methanotrophic bacteria whose presence in the landfill cover soil was predicted by the phylogenetic analysis of clone sequences. The initial detection of microbes via molecular methods is an important first step in community analysis, but detailed investigation into physiology is possible only when organisms are isolated in pure culture. One reason that diversity assessments based on culture-independent analyses have historically been quite different than those based on culturing is the phenomenon of competitive exclusion during enrichment (58). It has been recognized that rare but opportunistic bacteria tend to outcompete the numerically dominant, oligotrophic species under the typical set of enrichment conditions (11). However, in cultures diluted to extinction, the most abundant organisms become favored during enrichment since the opportunistic species may no longer be present in the highest dilutions. Our isolates may represent such species; they may be unfit to compete successfully with some of the more typically isolated methanotroph strains. Equally important is the ability of the enrichment to reproduce as closely as possible the resources and conditions in situ. Dedysh et al. (13, 14) recently had success isolating novel methane oxidizers by engineering the enrichment media and incubation parameters to more accurately simulate the natural conditions of acidic ombrotrophic peat bogs. We adopted a similar approach; methanotrophs living in landfill cover soil enjoy some of the highest levels of methane on the planet, so we used some enrichment series with relatively high (approximately 50%) methane concentrations in the headspace. Also, we adjusted the initial pH of some of the enrichment series to more accurately reflect the actual pH of the landfill soil. Interestingly, it seems the most important variable in determining the isolation of type I versus type II species in our sample was the strength of the medium. Type II species dominated enrichments in which the NMS medium was diluted fivefold (A, E, and F series) regardless of initial pH or methane concentration of the headspace. This suggests a propensity for type II species to better acquire nutrients when they are more scarce. Alternatively, they may be sensitive to the higher salt concentration of the full-strength medium, rendering them at a selective disadvantage.

The results described here add to the growing body of evidence suggesting that the formally described methanotrophs are but a subset of the actual diversity of this physiological type. Previous research using phylogenetic probes and primers directed against the methanotrophs has also detected novel methanotroph sequences. Holmes et al. (28) discovered an unusual 16S rDNA sequence from organisms related to the genus Methylomonas in seawater methane enrichments. Organisms containing this sequence were visualized by in situ hybridization and found to be quite numerous (45% of all cells) in the enrichment, although they could not be obtained in pure culture. McDonald et al. (38) investigated methanotroph diversity in peat cores and found 16S rDNA clone sequences related to but distinct from the characterized type II methanotrophs that may represent novel acidophilic species. Culture-independent diversity assessments have also been performed by exploiting certain conserved functional genes. McDonald et al. (39) used primers specific for the mmoX gene (which codes for the alpha subunit of the hydroxylase component of the sMMO) and presented work that suggests that a large number of unusual methanotrophs, with mmoX sequences different from those of the extant species, are present in the peat samples. Similar results were obtained from peat samples by using the gene for the large subunit of the methanol dehydrogenase, mxaF (40), and the pmoA gene (41). We have some evidence suggesting that our novel type II methanotroph isolates are related to some of the organisms detected in the suite of molecular ecology experiments performed by McDonald and coworkers on acidic peat samples. As seen in Fig. 4, the PmoA amino acid sequences of AML-A3 and AML-A6 are highly similar to clone PD4, a clone sequence retrieved from the peat (41). However, the novel 16S rDNA clones retrieved from the same samples diverge significantly from our isolates: Moorhouse peat core clones MHP14 and MHP17 were each <94% identical to both AML-A3 and AML-A6 (38). It remains to be seen whether the organisms isolated here can account for some of the molecular methanotroph diversity observed in peat. Although both types of environments are acidic, the pH of the peat bog (3.6) is more extreme than that of the landfill soil. Furthermore, one may expect that methanotrophs adapted to the high methane levels and unique soil chemistry prevalent in landfill soil differ from species that thrive in organic-rich peat.

At first glance, the diversity assessment via DGGE analysis seems to be the most encompassing of the three techniques employed here. DGGE profiles of the type I and type II methanotrophic communities resulted in distinct banding patterns that were not too complex, as is often the case when universal- or domain-specific PCR primers are used (45). We found that only some of the bands present in the community profile could be accounted for by the clones and isolates, suggesting that some species were not detected by cloning and sequencing or culturing. However, it is likely that not all bands in the profiles correspond to actual 16S rRNA sequence types. The formation of heteroduplex molecules is expected to be a problem with the community analysis of a highly related phylogenetic cluster, since the mixed PCR products of closely related species may have enough sequence similarity to anneal together. We noted that with the DGGE analysis of both the type I and type II community members, the clones and isolates always accounted for bands that melted at the higher denaturant concentrations. It is possible that bands that denature at the lower concentrations (upper bands on the gel) are due to heteroduplex formation, although migration could also be retarded by secondary structure or other unknown associations. Clearly the diffuse bands A and B in the type I profile are the result of an artifact that occurs with the mixed template DNA, as DNAs reamplified and cloned from these excised bands migrated to a position of much higher denaturant concentration when reanalyzed by DGGE. Also of note, some clones and isolates migrated to positions not represented on the DGGE profiles. For example, isolate AML-E13 melted at a denaturant concentration higher than any band seen in the type II community profile (Fig. 7). Clearly caution should be exercised when making diversity judgments based on DGGE banding patterns.

The two novel type I isolates are part of a monophyletic line of descent and are seemingly just the culturable members of a larger phylotype present in the landfill soil. This phylotype may represent a group of organisms that are especially well adapted to this habitat, since no other type I sequence was retrieved. In contrast, both the clone-based and culturing assessments suggested that the type II methanotroph species were much more diverse, as several distinct clusters of clones and isolates were observed. Evidently the characteristics of the landfill soil support a broad range of type II species. Our future plans include a formal characterization of our unique isolates in order to determine their valid taxonomical status. Whether these groups are different enough to warrant the status of new genera will depend on further physiological, morphological, and genetic tests.