APPLIED AND ENVIRONMENTAL MICROBIOLOGY, July 2005, p. 3826–3831
0099-2240/05/$08.00⫹0 doi:10.1128/AEM.71.7.3826–3831.2005
Copyright © 2005, American Society for Microbiology. All Rights Reserved.
Vol. 71, No. 7
Diversity of Methanotrophic Bacteria in Tropical Upland Soils under
Different Land Uses
Claudia Knief,1,2 Supika Vanitchung,3 Narumon W. Harvey,3 Ralf Conrad,1 Peter F. Dunfield,1,4
and Amnat Chidthaisong3*
Received 10 October 2004/Accepted 2 February 2005
Three upland soils from Thailand, a natural forest, a 16-year-old reforested site, and an agricultural field,
were studied with regard to methane uptake and the community composition of methanotrophic bacteria (MB).
The methane uptake rates were similar to rates described previously for forest and farmland soils of the
temperate zone. The rates were lower at the agricultural site than at the native forest and reforested sites. The
sites also differed in the MB community composition, which was characterized by denaturing gradient gel
electrophoresis (DGGE) of pmoA gene fragments (coding for a subunit of particulate methane monooxygenase)
that were PCR amplified from total soil DNA extracts. Cluster analysis based on the DGGE banding patterns
indicated that the MB communities at the forested and reforested sites were similar to each other but different
from that at the farmland site. Sequence analysis of excised DGGE bands indicated that Methylobacter spp. and
Methylocystis spp. were present. Sequences of the “forest soil cluster” or “upland soil cluster ␣,” which is
postulated to represent organisms involved in atmospheric methane consumption in diverse soils, were
detected only in samples from the native forest and reforested sites. Additional sequences that may represent
uncultivated groups of MB in the Gammaproteobacteria were also detected.
anotrophic bacteria (MB). Seven recognized genera of MB
belong to the group containing the type I methanotrophs
(Gammaproteobacteria), while the group containing the type II
methanotrophs consists of four genera of MB (Alphaproteobacteria). The enzyme methane monooxygenase catalyzes the first
step in methane oxidation. With the exception of Methylocella
(6, 7, 9), all MB possess the particulate form of this enzyme
(particulate methane monooxygenase [pMMO]). The pmoA
gene, encoding the active site subunit of the pMMO, is therefore a specific and almost universal marker gene for methanotrophs and has often been targeted by cultivation-independent methods to characterize the MB communities in different
soils. Sequences closely related to the sequences of seven genera of MB have been detected by these methods in upland soils
(4, 12, 15, 29). The presence of some pmoA sequences indicated that uncultivated MB are present in these soils. Uncultivated organisms that harbor pmoA sequences of upland soil
cluster ␣ (USC␣) or upland soil cluster ␥ are most likely
involved in atmospheric methane oxidation in upland soils (16,
23). With the exception of one soil sample from a rainforest in
Brazil, in which USC␣ was detected (16), characterization of
soil methanotrophic communities has been restricted to upland soils from the temperate zone.
In the present study, we compared the methane oxidation
activities and methanotrophic community compositions of
tropical soils under different land uses, including a natural
forest site, a reforestation site, and a cornfield. The methane
oxidation activities and community compositions of these soils
were analyzed and compared with other data available for
temperate soils.
The current atmospheric mixing ratio of the greenhouse gas
methane (CH4) is 1.75 ppm by volume (8). An estimated 30 Tg
of CH4 year⫺1 is consumed via microbiological oxidation in
upland soils, accounting for about 6% of the global methane
sink (17). Atmospheric methane oxidation has been detected
in many different upland soils, including arctic and subarctic
tundra soils, grasslands and arable soils of the temperate zone,
tropical forest soils, savannah soils, and even arid desert soils
(25, 31). Most studies have been performed to estimate the
methane uptake capacity of upland soils of the temperate zone,
and few data are available for tropical and subtropical soils (10,
21, 22, 27, 28). Most of these data indicate that the methane
uptake rates of tropical and subtropical forest soils are comparable to those of forest soils of the temperate zone, but
higher oxidation rates have been reported for some tropical
soils (29).
Among upland soils, forest soils are much more efficient
methane sinks than cultivated soils (1, 3). Changes in land use,
especially cultivation of formerly undisturbed soils, reduce the
sink strength for atmospheric methane by 60 to 90% (30, 31).
Such reductions have been reported for tropical soils as well
(10, 21). However, the methane oxidation rate seems to recover much faster after abandonment of agricultural activities
(22) compared to systems in the temperate zone.
Methane oxidation in upland soils is mediated by meth* Corresponding author. Mailing address: Joint Graduate School of
Energy and Environment, King Mongkut’s University of Technology
Thonburi, 91 Pracha-Uthit Rd., Bangkok 10140, Thailand. Phone:
66-2-4708309. Fax: 66-2-8729805. E-mail: amnat_c@jgsee.kmutt.ac.th.
3826
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Max Planck Institute for Terrestrial Microbiology, Karl-von-Frisch Straße, 35043 Marburg, Germany1; Laboratoire des
Interactions Plantes Micro-organismes, INRA/CNRS, BP 52627, Chemin de Borde Rouge, 31326
Castanat-Tolosan, France2; Joint Graduate School of Energy and Environment, King Mongkut’s
University of Technology Thonburi, 91 Pracha-Uthit Rd., Bangkok 10140, Thailand3; and
Institute of Geological and Nuclear Sciences, Wairakei Research Centre, 114
Karetoto Rd., Taupo, New Zealand 164
VOL. 71, 2005
METHANOTROPHIC COMMUNITIES IN TROPICAL UPLAND SOILS
MATERIALS AND METHODS
Heidelberg, Germany) to bring the volume to 50 l. Mixed pmoA PCR products
were separated by DGGE. Visible bands were excised and reamplified. PCR
products from excised DGGE bands were purified and sequenced exactly as
described by Knief et al. (23).
Phylogenetic sequence analysis. Phylogenetic tree reconstructions were based
on deduced amino acid sequences of partial pmoA and amoA sequences and
were prepared with the ARB software package (24). The original tree construction included sequences of all DGGE bands, all available pmoA sequences in the
GenBank database (July 2004), and selected public domain amoA sequences.
Then 22 representative sequences from this study plus 38 public domain sequences were selected for analysis.
Cluster analysis. A cluster analysis was performed based on the presence or
absence of 21 different bands visible in DGGE gels of PCR products amplified
with primers A189-GC and A682 and with primers A189-GC and mb661. Jaccard
similarity coefficients were calculated, and a hierarchical tree was constructed
based on average linkage and Euclidean distances using SYSTAT, version 10.2
(SPSS Inc., Richmond, CA).
Isolation of methanotrophic bacteria. Diluted nitrate mineral salts medium at
a slightly acid pH (pH 5.8) was used to enrich for MB as described by Dunfield
et al. (9) with soil samples from forested sampling sites SK and AC.
Nucleotide sequence accession numbers. Representative pmoA nucleotide sequences obtained during this study have been deposited in the GenBank, EMBL,
and DDBJ nucleotide sequence databases under accession numbers AJ868266 to
AJ868287.
RESULTS
In situ atmospheric methane oxidation. Methane flux was
measured in March 2003 and in July 2003 (on the day that soil
samples were taken for molecular studies). Ten chambers were
used for flux estimates at site SK, while five chambers were
used at sites AC and CF. Only data from chambers with significant correlation of the measurement points (the Pearson
correlation coefficient of log-transformed flux data versus time
was significantly more than zero at the P ⫽ 0.05 level) were
taken into account for calculation of the average methane flux.
Thus, the average values given below for site SK were based on
the data from only five chambers in March and six chambers in
July, and the average values for sites AC and CF were based on
four chambers in March and three chambers in July. Net atmospheric methane consumption was observed at sites SK and
AC. At site CF net oxidation of methane was observed only in
March. The methane uptake rates obtained from different
chambers at the same sampling site showed large variations.
Not all chambers at a site showed net consumption of methane. Likewise, in some chambers neither net emission nor net
consumption was observed. The net methane fluxes at site SK
ranged from ⫺4.4 to ⫺0.6 mg CH4 m⫺2 day⫺1 in March and
from ⫺0.2 to ⫺1.2 mg CH4 m⫺2 day⫺1 in July. At site AC, the
net methane fluxes ranged from ⫺0.9 to ⫺1.8 mg CH4 m⫺2
day⫺1 in March and from 2.7 to ⫺5.6 mg CH4 m⫺2 day⫺1 in
July; and at site CF the values ranged from ⫺1.4 to 1.4 mg CH4
m⫺2 day⫺1 in March and from 0.3 to 1.4 mg CH4 m⫺2 day⫺1 in
July. A negative flux indicates net consumption, while a positive flux indicates net emission. To test for significant differences in the net methane fluxes for the sampling sites, the
nonparametric Mann-Whitney test was used. For this comparison, the flux data for both forested sites for both months were
combined and compared to the data for the farmland site. The
results of this analysis indicate that the net methane fluxes at
the two forested sites were significantly different (more negative) than the flux at the CF site (P ⬍ 0.01).
Characterization of the methanotrophic communities. Using cultivation-independent methods, the MB communities
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Sampling sites. Three adjacent sampling sites were located in Amphur Wang
Nham Keaw, Nakorn Ratchasrima province in Thailand. The forest site (site SK)
was a natural dry evergreen forest within the Sakerat Experimental Station. The
dominant tree species were Hopea ferrea, Pterocarpus marcrocarpus, Xylia xylocarpar, Dalbergia cochinchinensis, Lagerstroemia duppereana, and Shorea henryana. The reforestation site (site AC) was located about 5 km from site SK. It was
planted with fast-growing, nitrogen-fixing tree species in 1988. The studies were
performed on a plantation of Acacia mangium. Before reforestation, this site was
used as farmland (corn and cassava). The third sampling site was a cornfield (site
CF) located adjacent to the restoration area (2 km away). It was deforested more
than 40 years ago, and corn has been continuously cultivated at this site for the
last 16 years. The soils at sites SK and AC were highly acidic (pH 4.2, 1:1 in
water), while the pH at site CF was 5.6. The soil texture at site SK is clay (clay
content, 51%), and at sites AC (clay content, 30%) and CF (clay content, 21%)
the texture is sandy clay loam. Soil preparation at the CF site started in mid-June
2003, and seeds of corn were sown on 10 July 2003. On this date, chemical
fertilizer (16-20-0, N-P2O5-K2O) was applied at a rate of 50 kg ha⫺1. Soil samples
for molecular analysis were taken from a depth of 10 to 20 cm on 27 and 28 July
2003.
Methane oxidation activity. The net methane flux across the soil surface was
determined in March and July 2003 using a closed static chamber method. The
chambers consisted of a top made of transparent acrylic glass (30 cm wide by 30
cm long by 15 cm high) that could be attached to a fixed collar made of stainless
steel. The collar was inserted 10 to 15 cm deep into the soil and remained there
during the whole study period. The chambers were 10 to 15 m from each other.
During measurement, the chamber top was inserted into a 1-cm-deep waterfilled channel of the fixed collar. Using 30-ml syringes inserted through silicon
stoppers in the chamber lids, 6 to 10 25- to 30-ml gas samples were taken from
each chamber during the 1 h after capping. Methane mixing ratios of the gas
samples were determined with a Shimadzu gas chromatograph (model 14B)
equipped with a flame ionization detector and an Unibead C packed column
(injector temperature, 120°C; oven temperature, 100°C; detector temperature,
300°C). The first-order uptake rate constant was estimated from the exponential
decrease in methane over time. The methane oxidation rate was calculated from
the first-order uptake rate constant by multiplication with the initial methane
mixing ratio in the chamber headspace.
DNA extraction. DNA was extracted from 0.5 g of soil using a Fast DNA SPIN
kit (Bio 101, La Jolla, CA) according to the manufacturer’s instructions, with
modifications. Cell lysis was performed with a cell disruptor (FP 120 FastPrep;
Savant Instruments Inc., Farmingdale, NY) operating at 6.5 m s⫺1 by using two
45-s cycles. After centrifugation (20,000 ⫻ g, 10 min) the supernatant was collected, and the pellet containing soil and beads was resuspended in buffers
supplied with the kit for a second DNA extraction. Proteins and cell debris were
precipitated as described in the manufacturer’s instructions, and 1 ml of binding
matrix was added to the supernatant. For purification, the matrix-bound DNA
was washed three times with 1 ml of a 5.5 M guanidine isothiocyanate solution
(modified as described by Yeates and Gillings [33]). After the last centrifugation
step (14,000 ⫻ g, 1 min) the supernatant was removed, and the matrix-bound
DNA was suspended in 0.6 ml of a guanidine isothiocyanate solution and loaded
onto SPIN filters supplied with the kit. Final elution of the DNA from the filters
was performed twice with 100 l of DNase-free water. DNA extracts were
purified with polyvinylpolypyrrolidone and a QIAquick PCR purification kit
(QIAGEN, Hilden, Germany) (23).
PCR amplification and denaturing gradient gel electrophoresis (DGGE). A
partial fragment of the pmoA gene was PCR amplified with primer A189 with a
GC clamp (12) in combination with either primer A682 (15) or primer mb661
(5). A touchdown PCR program (12) with annealing temperatures decreasing
from 64 to 57°C was used for 35 cycles. A fragment of the mmoX gene encoding
the active site subunit of soluble methane monooxygenase (sMMO) was amplified with a newly designed forward primer, mmoXf945 (5⬘-TGG GGY GNA
ATC TGG AT-3⬘), and reverse primer mmoXB1401 of Auman et al. (2). A GC
clamp described by Iwamoto et al. (18) was attached to the 5⬘ end of primer
mmoXf975. The PCR program consisted of an initial denaturation step of 5 min
at 94°C, followed by 35 cycles of 94°C for 1 min, 63 to 56°C for 1 min, and 72°C
for 1 min and then a final extension step of 72°C for 7 min.
All PCR mixtures contained each primer at a concentration of 1.0 M, 5 l of
Accutaq-LA 10⫻ buffer (Sigma-Aldrich, Taufkirchen, Germany), 3.5 mM
MgCl2, 25 g of bovine serum albumin (Roche Diagnostics GmbH, Mannheim,
Germany), each deoxynucleoside triphosphate (Promega, Mannheim, Germany)
at a concentration of 200 M, 2.5 U of REDAccuTaq LA DNA polymerase
(Sigma-Aldrich), 1 l of template DNA, and enough sterile water (Q-Biogene,
3827
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KNIEF ET AL.
APPL. ENVIRON. MICROBIOL.
TABLE 1. PmoA sequence types detected at the different sampling sitesa
Site SK
Site AC
Site CF
Detected taxon
A682b
Ammonia oxidizers (AmoA)
Cluster 2 (PmoA/AmoA)
Methylobacter
Cluster 3
Methylocystis
USC␣
Cluster 5
a
⫹
⫹
mb661
⫹
⫹
⫹
⫹
A682b
⫹
mb661
A682b
mb661
⫹
⫹
⫹
⫹
⫹
⫹
⫹
⫹
⫹
⫹
⫹
⫹
Phylogenetic positions of the different taxa are shown in Fig 1.
sites SK and CF. These “cluster 2” sequences exhibited 88 to
97% identity to a sequence previously recovered by cultivationindependent methods from a temperate forest soil, represented by DGGE band E5FB-f (23). Sequences that were phylogenetically most closely related to amoA genes of ammoniaoxidizing bacteria were detected only at site CF.
Isolation of MB from forested sites. The methanotrophic
isolate sakb1 was isolated from site SK, while isolate arc2 was
obtained from site AC. Based on the partial pmoA gene sequences, these isolates were identified as Methylocystis spp.
(Fig. 1). This result was confirmed by 16S rRNA sequence
analysis and by the morphology of the isolates. The pmoA
sequences of the isolates from site AC were not identical to the
pmoA sequences that were detected in this soil by cultivationindependent methods. At site SK, pmoA sequences that indicated the presence of Methylocystis spp. were not detected.
Relationship between sampling site and community composition of methane-oxidizing bacteria. The DGGE banding pattern of PCR products obtained with both backward primers
indicated that there were clear differences in the community
compositions of methane-oxidizing bacteria at the different
sampling sites. The duplicates analyzed from each sampling
site were very similar to each other, as demonstrated by the
results of a cluster analysis performed based on the DGGE
banding pattern (Fig. 2). The duplicates from all soil samples
formed separate clusters. The MB community similarity between sites SK and AC was greater than the similarity of either
site SK or site AC to site CF.
DISCUSSION
In recent years, several studies have examined the methane
oxidation activity together with the structure of the methanotrophic community of diverse upland soils (13, 16, 19, 23,
26). With the exception of a Brazilian rainforest soil (16), all
data on methanotrophic community structure are data for upland soils of the temperate zone of the Northern Hemisphere.
Because some tropical sites have much higher rates of methane
oxidation than temperate sites (27, 28, 29), it is of interest to
investigate the MB community composition in these areas.
The measured methane uptake rates of the Thailand soils
(up to ⫺5.6 mg CH4 m⫺2 day⫺1 at site AC) were similar to
rates published previously in several other studies of upland
soils (up to ⫺7 mg CH4 m⫺2 day⫺1) but were not as high as the
highest rates reported for some tropical forest soils (up to ⫺14
mg CH4 m⫺2 day⫺1) (27, 28). Both forested sites (sites SK and
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were characterized by using soil samples taken from a depth of
10 to 20 cm during the second half of the wet season. Duplicate
soil samples were taken from each sampling site. The pmoA
gene fragment, which was used as a functional marker for
characterization of the methanotrophic communities, was successfully PCR amplified from all soil DNA extracts. A fragment of the mmoX gene could not be amplified from any
sample. Two different reverse primers were used for amplification of the pmoA gene fragment. Primer A682 is the less
specific of the two, since it was designed to amplify both pmoA
and amoA gene fragments (15). Primer mb661 was designed to
amplify pmoA gene fragments specifically and did not amplify
amoA gene fragments (5).
The recovery of PmoA sequences very closely related to
sequences from isolates of Methylocystis and Methylobacter indicated that well-known cultivated genera of MB were present
at all sites (⬎96% amino acid identity) (Table 1). Sequences of
the USC␣, which probably represented uncultivated MB, were
detected at sites SK and AC (98% identity) but not at site CF.
Likewise, pmoA sequences belonging to a group that was a
closely related to but clearly distinct from previously detected
USC␣ sequences (cluster 5) were detected in these two soils
but not at site CF. Cluster 5 sequences AC-A1, AC-A2, and
SK-B in the phylogenetic tree (Fig. 1) exhibited maximum
levels of identity of 81% to USC␣ sequences, represented by
EL4-a in Fig. 1. While USC␣ sequences were obtained only
when primer A682 was used in PCRs, the novel sequence type
was detected only when primer mb661 was used.
Another PmoA sequence type that was indicative of another
taxon of uncultivated MB was detected at all sampling sites.
PmoA sequences of this “cluster 3” formed two separate
branches, which were distantly related to sequences of MB in
the Gammaproteobacteria. The levels of amino acid identity of
PmoA sequences in these branches were 93% to each other, 93
to 97% to sequences of the uncultivated bacteria represented
by “clone Zhenjiang 5” and “clone Beijyuan 2,” and 87 to 93%
to sequences of cultivated methanotrophs of the genera Methylococcus and Methylocaldum. Since the amino acid identity of
these novel sequences was approximately equal to that observed for PmoA sequences from members of both genera
(Methylococcus and Methylocaldum), the phylogenetic relationship could not be resolved and is represented by a multifurcation in the tree (Fig. 1).
Sequences whose phylogenetic position was intermediate
with respect to sequences belonging to clearly definable AmoA
or PmoA sequence types were detected in soil samples from
VOL. 71, 2005
METHANOTROPHIC COMMUNITIES IN TROPICAL UPLAND SOILS
3829
AC) showed net methane uptake, but only weak methane
uptake or even net methane emission was observed at site CF.
This indicates that some parts of the soil profile might have
been saturated with water to the level that methanogenesis
developed and overloaded the total methane oxidation potential. Although the study was not blocked in order to rule out
spatial effects, this general trend agrees well with previous
studies indicating that the conversion of natural forest sites to
farmland leads to a 60 to 90% reduction in the atmospheric
methane uptake rate but that the activity recovers at reforested
sites (21, 29, 32). In addition, it has been found that the oxidation rates of tropical soils recover much faster after aban-
donment of agricultural activities than the oxidation rates of
temperate systems recover (22, 29). This may explain why the
methane oxidation rate at reforestation site AC was comparable to the rate at site SK, although site AC was reforested only
16 years ago.
Fragments of the pmoA gene were amplified from all soil
DNA extracts, but mmoX genes were not recovered from the
soil samples. This is in accordance with results obtained for
upland soils of central Europe (23). Either the dominant MB
in upland soils do not possess mmoX genes or this assay has a
higher detection limit than the pmoA assay. The former possibility is reasonable considering that MB in upland soils have
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FIG. 1. Phylogenetic tree based on deduced amino acid sequences of partial pmoA and amoA sequences, showing the relationship of sequences
detected at the different Thailand sampling sites to sequences of pure MB cultures and sequences detected in other cultivation-independent
studies. Sequences from this study are indicated by boldface type and are designated according to the sites (SK, native forest; AC, reforestation;
CF, cornfield). Sequences recovered from PCR products that were amplified using the A682 reverse primer are indicated by lowercase letters, while
uppercase letters indicate sequences from PCR products that were obtained using the mb661 reverse primer. PmoA sequences of two methanotrophic isolates obtained from soils at sites SK and AC (sak1b and arc2) were also included. The tree was calculated based on 146 amino acid
positions using the Treepuzzle algorithm with the Jones-Taylor-Thornton evolutionary model (20). The positions of recovered PmoA and AmoA
sequences in the tree were confirmed by the topology of a neighbor-joining tree. The solid circles indicate branches that were present in 90% of
25,000 reconstructed Treepuzzle trees, and the open circles indicate branches that were present in 80% of the trees. AmoA sequences of
ammonia-oxidizing bacteria were used as an outgroup. Bar ⫽ 0.10 change per amino acid position.
3830
KNIEF ET AL.
to live on very low substrate concentrations. Under these oligotrophic conditions it should be preferable to use pMMO
rather than sMMO, since it has a lower energy demand for the
oxidation of methane to methanol. MB expressing pMMO
have higher growth yields and show a higher affinity for methane than MB expressing sMMO (11).
The only known genera of MB detected in the Thailand soil
samples were Methylocystis and Methylobacter. While Methylocystis has been detected in several different upland soils (4, 16,
23, 26, 30), Methylobacter has been detected only in an acidic
heathland soil (4). Some Methylocystis spp. were also isolated
from the soils, although interestingly, based on PmoA phylogeny the strains were not the same strains detected by cultivation-independent methods in the soil samples. This result emphasizes the fact that both molecular and cultivation methods
are subject to inherent biases.
Unusual sequences obtained from several DGGE bands indicated that different taxa of uncultivated putative methanotrophs were also present in the soil samples. Organisms
harboring pmoA sequences of USC␣ have been detected previously in several upland soils, including acidic tropical forest
soils (16). Such sequences were present at sampling sites SK
and AC, as were sequences that represent cluster 5, which is
closely related to USC␣. Cluster 3 sequences represent a group
of uncultivated type I methanotrophs related to Methylocaldum
and Methylococcus. A further cluster of PmoA sequences
within this broad Methylococcus-Methylocaldum group (type X
MB) is formed by sequences that were detected in different
rice field soils (clone Beiyuan 2 and clone Zhenijang 5) (14).
Thus, there seem to be diverse uncultivated MB taxa which
have (on the PmoA level) a phylogenetic position between
Methylocaldum spp. and Methylococcus spp. So far, the detection of a third cluster representing uncultivated bacteria, cluster 2, has been restricted to upland soils. Since the sequences
of this branch are only distantly related (⬍69%) to PmoA
sequences of recognized genera of MB, the possibility that
these sequences code for the AmoA of uncultivated ammoniaoxidizing bacteria cannot be excluded.
The different land uses at the sampling sites were reflected
by different methane uptake rates and different soil pHs, as
well as by different methanotrophic communities, especially for
the cornfield soil. The pmoA sequences of USC␣ and cluster 5
were detected in samples from sites SK and AC but not in the
soil samples from the cornfield. The absence of USC␣ at site
CF is in agreement with results of other studies, in which the
methanotrophic communities of some farmland soils were analyzed and in which USC␣ sequences were not detected, although they were present in adjacent grassland and forest soils
(23). Although the organisms harboring USC␣ sequences appear to occur more frequently in acidic soils than in soils with
a neutral pH, they do occur in soils at a wide pH range (pH 4.0
to 8.0) (23), so their absence from the farmland soil is probably
not the result of a pH shift alone. Other sequences that led to
the different community compositions at the different sampling
sites were sequences of Methylocystis spp., cluster 2, and ammonia-oxidizing bacteria (Table 1). Sequences of Methylobacter and cluster 3 were detected at all sampling sites. A
cluster analysis was used to verify the differences numerically.
The resulting cluster diagram confirmed the high similarity of
replicate samples from one sampling site and differences between the sampling sites (Fig. 2). The differences within the
replicate samples from one site were due to faint DGGE bands
visible in one sample but not in the other samples. Thus, pmoA
sequences with abundance near the detection limit of the
methods were mainly responsible for the dissimilarity of duplicate samples. The main purpose of this cluster analysis was
to compare the different sampling sites. The community compositions at sites SK and AC were more similar to each other
than either was to the community composition at site CF. This
finding is in accordance with the methane uptake rates and
pHs of the sampling sites, which also indicated a high degree of
dissimilarity between site CF and sites SK and AC.
These data suggest that land use changes are connected not
only to changes in the methane uptake capacity of soils but also
to changes in the community composition of methane-oxidizing bacteria. The change in the community composition may be
an important factor leading to the general decrease in the
methane uptake rate of farmland soils. To understand the
effects on land use and to confirm our findings, however, further studies on the relationship among land use, MB community composition, and the in situ methane uptake rate are
needed.
It is noteworthy that the community composition at reforested site AC represents a kind of intermediate state between
the communities at sites SK and CF. Since the community
composition and the methane uptake activity at reforested site
AC before the site was reforested are not known, we cannot
conclude whether the community that is there today redeveloped or whether the community structure was not drastically
changed after deforestation.
ACKNOWLEDGMENTS
This work was supported by the Thailand Research Fund (grant
MRG4580019) and the Deutsche Forschungsgemeinschaft (grant DU
377/1-1).
We thank Chongrak Watcharinrat of Kasetsart University for providing his experimental plots for soil sampling and Nathapol Lichaikul
of the Joint Graduate School of Energy and Environment for sampling
assistance and analysis. The Sakaerat Environmental Research Station
(Ministry of Science and Technology) and the Re-Afforestation Research and Training Station (Ministry of Natural Resources and Environment) kindly permitted access to the experimental sites and other
facilities.
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FIG. 2. Cluster analysis based on the presence or absence in
DGGE gels of 21 bands from PCR products obtained with primers
A189-GC and A682 and with primers A189-GC and mb661. Jaccard
similarity coefficients were calculated, and a hierarchical tree was constructed based on average linkage and Euclidean distances.
APPL. ENVIRON. MICROBIOL.
VOL. 71, 2005
METHANOTROPHIC COMMUNITIES IN TROPICAL UPLAND SOILS
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