Methanotroph populations and CH4 oxidation potentials in high-Arctic peat are altered by herbivory induced vegetation change

ABSTRACT Methane oxidizing bacteria (methanotrophs) within the genus Methylobacter constitute the biological filter for methane (CH4) in many Arctic soils. Multiple Methylobacter strains have been identified in these environments but we seldom know the ecological significance of the different strains. High-Arctic peatlands in Svalbard are heavily influenced by herbivory, leading to reduced vascular plant and root biomass. Here, we have measured potential CH4 oxidation rates and identified the active methantrophs in grazed peat and peat protected from grazing by fencing (exclosures) for 18 years. Grazed peat sustained a higher water table, higher CH4 concentrations and lower oxygen (O2) concentrations than exclosed peat. Correspondingly, the highest CH4 oxidation potentials were closer to the O2 rich surface in the grazed than in the protected peat. A comparison of 16S rRNA genes showed that the majority of methanotrophs in both sites belong to the genus Methylobacter. Further analyses of pmoA transcripts revealed that several Methylobacter OTUs were active in the peat but that different OTUs dominated the grazed peat than the exclosed peat. We conclude that grazing influences soil conditions, the active CH4 filter and that different Methylobacter populations are responsible for CH4 oxidation depending on the environmental conditions.


INTRODUCTION
High-Arctic peatlands store large amounts of organic carbon that is a source for microbial production of the greenhouse gas methane (CH 4 ). As a result of climate change, these peatlands are exposed to increased temperatures, changes in precipitation, herbivory and vegetation composition that might lead to increased CH 4 production rates (Parish et al. 2008;Sjögersten et al. 2011). Methane oxidizing bacteria (MOB), or methanotrophs, act as the dominant biological CH 4 filter in peat soils, consuming CH 4 produced in deeper anaerobic peat before it is released to the atmosphere (Reay, Smith and Hewitt 2007). MOB are a diverse group of bacteria, found within the classes Gammaproteobacteria, Alphaproteobacteria and Verrucomicrobia (Hanson and Hanson 1996;Knief 2015). The abundances and distribution of most MOB can be assessed by quantification and analysis of the pmoA gene which encodes the β-subunit of the particulate CH 4 monooxygenase (McDonald et al. 2008;Knief 2015). A broad diversity of MOB has been identified using pmoA, making it possible to evaluate the habitat preferences of different MOB (Knief 2015). Many cold ecosystems with a neutral pH are found to be dominated by MOB within Gammaproteobacteria (Wartiainen, Hestnes and Svenning 2003;Börjesson, Sundh and Svensson 2004;Wartiainen et al. 2006;Martineau, Whyte and Greer 2010;Graef et al. 2011). Among these, MOB within the genus Methylobacter are identified as the main CH 4 oxidizers in many freshwater wetlands (Yun et al. 2010;Tveit et al. 2013;Singleton et al. 2018;Smith et al. 2018;Zhang et al. 2019). Members of this group and other gammaproteobacterial MOB were also found in association with Sphagnum sp. mosses and vascular plants in a temperate peatland with their composition and activities being directly related to the plant biodiversity (Stępniewska et al. 2018). Methanotroph communities and their activities are known to be influenced by CH 4 concentration, pH, O 2 concentration, temperature, nitrogen concentration and copper availability (Amaral and Knowles 1995;Semrau, DiSpirito and Yoon 2010;Ho et al. 2013). It has been suggested that O 2 distribution plays a crucial role and may explain niche-adaptation in freshwater lakes (Biderre-Petit et al. 2011;Blees et al. 2014;Oshkin et al. 2015;Mayr et al. 2020) and flooded paddy soils (Reim et al. 2012). However, the ecology of large OTU numbers within e.g. Methylobacter and other gammaproteobacterial MOB (Tsutsumi et al. 2011;He et al. 2012;Beck et al. 2013;Oshkin et al. 2014;Knief 2015;Oswald et al. 2015;Bornemann et al. 2016), is mostly unknown. As a result, it is still difficult to explain the co-existence of many closely related OTUs within a defined ecosystem.
Grazing by geese and reindeer reduces the biomass of grasses and herbs. Warmer winters in temperate regions, increased food availability due to changes in agriculture and protection from hunting has led to an increase in the total geese population (Hessen et al. 2017). In Solvatn (NyÅlesund, Svalbard, Northern Norway) experimental peat plots protected from geese herbivory by fences doubled the vegetation over the course of nine years, leading to increased peatland carbon uptake (Sjögersten et al. 2011). During peat formation, the plant cover and its roots influence the physical properties of the soil such as porosity and pore direction (Kruse, Lennartz and Leinweber 2008). In addition, root exudates stimulate microbial communities within the soil and the exudates from different plant types (Bardgett et al. 2013), potentially create niches for different microorganisms. Thus, herbivory or its absence, may have a substantial effect on the soil structure, biology and chemistry.
Solvatn and adjacent peatlands close to Ny-Ålesund have been studied thoroughly during the last 15 years with emphasis on the CH 4 cycle, showing that substantial potentials for CH 4 production and oxidation exist in these soils (Høj, Olsen and Torsvik 2005;Graef et al. 2011;Tveit et al. 2013Tveit et al. , 2015. However, the effect of changes in herbivory on the CH 4 cycles were not studied. Here, in a comparison of 18-year old exclosures (Sjögersten et al. 2011) and nearby grazed sites, we have addressed how the microbial CH 4 filter is affected by intensive herbivore grazing over years. Specifically, we investigated the relationship between altered soil properties, potential CH 4 oxidation rates and the active methanotroph communities by 16S rRNA gene and pmoA transcript amplicon analyses.

Field site and sampling
The Solvatn peatland (N78 • 55.550, E11 • 56.611) is located close to NyÅlesund, Svalbard. It is heavily grazed by Barnacle geese (Branta leucopsis) and is dominated by brown mosses, primarily Calliergon richardsonii (Solheim, Endal and Vigstad 1996). Exclosures established in 1998 protect parts of the peatland vegetation from geese grazing (Sjögersten et al. 2011) allowing growth of vascular plants that are otherwise suppressed by grazing (Fig. 1). Two sampling sites from the Solvatn peatland were selected (SV1 and SV2), both of which were used by Sjögersten et al. (2011). Each site includes an exclosed plot and an adjacent grazed plot. Two field campaigns were conducted in summer, during the active growing season (August 2015 and 2016), while one field campaign was conducted immediately after snowmelt (June 2016). Below, we refer to these time points as summer 2015, spring 2016 and summer 2016.
In each plot, two blocks (approx. 30 × 30 × 20 cm) were cut from the peat soil and kept cool throughout transportation to the on-site laboratory, approximately 600 m away from the field site. Each block was separated in three vertical sections designated A, B and C (approx. 30 × 10 × 20 cm).
Section A was frozen at −20 • C and transported to the laboratory at UiT, The Arctic University of Norway, where it was used for the determination of water content and soil organic matter (SOM).
Section B and C were then divided in seven horizontal layers (0.5-8 cm for the upper six layers, 8-12 cm for the lowest layer), which served as material for the further analyses. The top layers (soil surface) of all plots were composed only of plants, whereas the layers two to seven were composed of partly decomposed peat. In the exclosed plots, the top 2-3 cm below the vegetation was a mixture of roots and peat soil. In the grazed plots, few or no living roots were observed.
Section B layers were used to measure CH 4 oxidation potentials ex situ (see next section). At the end of these measurements, peat samples from each microcosm were collected in 15 ml plastic tubes (VWR High-Performance polypropylene centrifuge tubes), flash frozen in liquid nitrogen (N 2 ) and stored at −80 • C.
Section C layers were transferred to sterile 15 ml plastic tubes (VWR High-Performance polypropylene centrifuge tubes), flash frozen in liquid N 2 immediately after arrival on the on-site laboratory and stored at −80 • C.
All soil samples from section B and C were shipped to the laboratory at UiT, the Arctic University of Norway, and stored at −80 • C until further processing. An overview of the sampling design and the respective analyses for each sampling is provided in Table S1 (Supporting Information).

Environmental characterization
Prior to soil water content and SOM analysis, section A from each sampling campaign was thawed in a cold room (8 • C) and separated into horizontal layers as described for sections B and C. Soil water content was determined gravimetrically by drying 10 g of peat at 150 • C over night. The dried peat soil was then incinerated at 450 • C and the amount of burnt peat matter was determined gravimetrically to deduce the amount of SOM.
O 2 concentration and temperature were measured in situ, using an optical O 2 sensor and thermometer (Fibox 4 Optode, Presens, Germany). Measurements were taken at the soil surface and at 5 cm intervals down to 20 cm depth.
To measure in situ CH 4 concentrations, pore water samples were extracted at 5, 10, 15 and 20 cm depth below the vegetation as described in Liebner et al. (2012). Briefly, we extracted 5 ml pore water using perforated brass rods and injected the pore water into 20 ml serum vials, which had been added 0.1 ml 1 M HCl and flushed with N 2 . Headspace CH 4 concentrations in these vials were measured using a GC-FID (SRI Instruments, CA, USA). Gas samples were retrieved using a pressure tight syringe (Vici Precision Sampling, LA, USA) and injected directly onto a GC-FID with a HayeSep D packed column (SRI Instruments, CA, USA). The instrument sensitivity was set to its maximum and the elution time for CH 4 was 1.8 min. From the headspace concentrations we could estimate the mass of headspace CH 4 by the ideal gas law. Further, when accounting for the dissolved CH 4 at room temperature (21 • C) and serum vial pressure using Henrys law constant for solubility of CH 4 in water, the headspace CH 4 content inside the serum vials equals the pore water CH 4 content.

Microcosm experiment for potential CH 4 oxidation ex situ along soil gradients
To measure potential CH 4 oxidation, approximately 15 g of each peat soil layer from section B were transferred to sterile 175 ml serum bottles and closed using Butyl rubber stoppers (Wheaton, Niemann et al. 2015) and aluminium crimp caps. CH 4 was added to obtain headspace concentrations of 0.5%-0.6% CH 4 (injection of 1 ml CH 4 , 100 v/v %). Such high concentrations were chosen to ensure CH 4 availability for the MOB during the incubation. We acknowledge a potential selective pressure towards low affinity MOB but we considered this bias as preferable to several perturbations caused by a large number of CH 4 injections or periods of CH 4 starvation. A volume of 34 ml air was added to obtain overpressure in the microcosms to enable easier sampling. Gas measurements were conducted from the headspace of the incubation bottles immediately after CH 4 injection followed by four subsequent time-points at regular intervals during a maximum of 45 h of incubation at 8 • C using a GC-FID (SRI Instruments, CA, USA). Details for the headspace sampling and the GC program are described in the section 'Environmental characterization' above. From the headspace CH 4 concentrations measured at each time point we calculated the CH 4 oxidation rate.

Nucleic acid extraction/16S rRNA gene and pmoA amplicon sequencing
Nucleic acids were extracted from the in situ peat soil layers (section C, spring and summer 2016). For extraction, we selected the layers with maximum CH 4 oxidation activity (0-2 cm depth in grazed plots, 4-8 cm depth in exclosed plots). From these extracts, we purified both DNA and RNA to identify the in situ bacterial community and active MOB community by 16S rRNA gene and pmoA transcript sequencing, respectively.
Additionally, nucleic acids were extracted from the samples collected and frozen at the end of the 45-hours incubation period (section B from summer 2015). In correspondence with the in situ peat soil samples, we selected layers with maximal CH 4 oxidation activity. From these extracts, RNA was purified and used for sequencing of pmoA transcripts. This was done to identify the active MOB community responsible for CH 4 oxidation during the microcosm experiment.
All samples were ground with mortar and pestle in liquid N 2 . Total nucleic acids were purified in duplicates from 0.2 g of each ground peat soil sample using a phenol/chloroform extraction protocol (Urich et al. 2008;Tveit et al. 2013). The duplicates of nucleic acids were mixed and then split in two samples, one for DNA purification and one for RNA purification.
DNA was purified by removing RNA with RNase A/T1 (Thermo Fisher Scientific, Waltham, MA/USA), followed by phenol/chloroform extraction and ethanol precipitation. Quality of DNA was assessed by Nanodrop and gel electrophoresis. DNA amplification was confirmed for the 16S rRNA gene using the 27F/1492R primer pair (Lane 1991). For 16S rRNA gene sequencing the V3-V4 region was targeted (Klindworth et al. 2013) using the Illumina MiSeq platform at IMGM Laboratories, Germany. The 16S rRNA gene amplicons were generated by a 2-step targetspecific (TS)-PCR using 1 ng DNA as template for 25 cycles followed by an 8-cycle index PCR using 1 μL TS PCR product as template. The Q5 R High Fidelity polymerase from NEB (Ipswich, MA, USA) was used for both PCRs and a negative control as well as a Mock community were amplified and sequenced in parallel to ensure sufficient quality.
To purify RNA, DNA was removed (RQ1 DNase, Promega), followed by RNA clean-up (MegaClear, Ambion) and ethanol precipitation. The RNA quality was assessed by Nanodrop and gel electrophoresis. RNA was reverse-transcribed (Superscript IV, Thermo Fisher) and the cDNA template was verified for the pmoA gene using the A189F/mb661R primer pair (Costello and Lidstrom 1999). The cDNA samples were sequenced using Illumina MiSeq and the two pmoA targeting primer pairs, A189F/mb661R and A189F/A682R (Holmes et al. 1995;Costello and Lidstrom 1999) at IMGM Laboratories, Germany. The pmoA gene amplicons were generated by a 2-step TS-PCR using 10 ng cDNA as template for 25 cycles followed by a 12-cycle index PCR using 1 μL from the TS PCR products. The polymerase used was the Q5 R High-Fidelity polymerase from NEB (Ipswich, MA, USA). Both a negative control and a Mock Community were amplified and sequenced in parallel to the samples to ensure sufficient quality.

Databases
Taxonomic assignment of OTUs for each of the three sequenced communities was done with a de-replicated database with sequences trimmed according to the primers used in this study. The sequences used for the pmoA database were retrieved from a published collection of pmoA sequences (Wen, Yang and Liebner 2016) and complemented with three Arctic Methylobacter sequences originating from Svalbard (GenBank id = AJ414658.1, KC878619.1, G7 Arctic mine isolate (genome not published)). The V3-V4 16S rRNA gene database was built from fragments of the SILVA 128 SSU database (Quast et al. 2013) (downloaded the 1st of October 2017). Both databases were trimmed according to the corresponding primers and de-replicated with a custom Perl script (https://github.com/cseppey/bin src my prog/tree/m aster/perl/sel db.pl).

Sequence data analyses
For each of the environmental sequence datasets, reads were merged using the program Flash (v. 1.2.8; (Magoč and Salzberg 2011)). Good quality sequences were filtered using a custom script (https://github.com/cseppey/bin src my prog/tree/maste r/cpp/qualCheck.cpp) by keeping only sequences without any window of 50 nucleotides with an average phred score below 20 prior to trimming the primers (https://github.com/cseppey/bin src my prog/tree/master/perl/trim primer.pl). Chimeras were removed using the program Vsearch (v. 2.4.4; (Rognes et al. 2016)) comparing the environmental sequences between them (de novo approach), as well as by comparing the sequences against the corresponding database (for pmoA primers: (Wen, Yang and Liebner 2016); for V3-V4 primer: SILVA 128). After trimming the primers the pmoA sequences were expected to start with the nucleotides 188-190 (TCG: serine) and finish with the nucleotides 658-660 (TAT: tyrosine) for the reversed primer mb661 or nucleotides 679-681 (TCG: serine) for the reversed primer A682R (Semrau et al. 1995). To avoid sequences containing frameshift mutations, thus incorrect open reading frames, sequences with a number of nucleotides not divisible by three and sequences containing a stop codon were removed.
OTUs were clustered from the processed environmental sequences using the program Swarm (v. 2.1.13; (Mahé et al. 2014)), and taxonomically assigned by using the best alignment between the dominant sequence of each OTU and the database using the program Ggsearch36 (v. 36.3.8f; (Pearson 2000)). The OTUs were finally selected according to their length (mb661: in order to remove obvious sequencing errors as well as to their taxonomic affiliation by discarding OTUs assigned to Archaea, chloroplast or mitochondria.

Statistical analyses
To reduce the noise caused by low relative abundances, we consider an OTU as absent of a sample if its relative abundance was < 0.001 in that sample. Prior to analyses, the three relative abundance community matrices were log normalized as previously described in (Anderson, Ellingsen and McArdle 2006) (function decostand, package vegan v. 2.5-2; (Oksanen et al. 2018)). The effect of factor (treatment i.e. grazing and sampling date), interaction between the factors and CH 4 rate, while removing the effect of sites, were assessed through redundancy analysis (RDA) (function capscale, package vegan v.2.5-2; (Oksanen et al 2018)). The significance of the factors, factors interaction and CH 4 rate, as well as the significance of the RDA axes were tested by a permutation test (10 000 permutations, function anova.cca, package vegan v. 2.5-2; (Oksanen et al. 2018)). To disentangle the effect of the interaction between grazing and sampling date, two other RDAs were calculated for each treatment. For each new RDA, the effects of sampling date, CH 4 oxidation rate as well as the RDA axes were tested as for the RDA performed on the two treatments together.
The most representative OTUs of each treatment (bioindicators) were assessed using an indicator species analysis (indval; function indval, package labdsv v. 1.8-0; (Roberts 2016)) on the relative abundance community matrices. For each OTU in each treatment, a score is calculated, which is maximized if (i) the OTU is mostly found in the given treatment (high specificity) and (ii) is found in all samples of the given treatment (high fidelity). An OTU was selected as a bioindicator if the probability of a higher indicator value was < 0.001 on 10 000 permutations. All statistical analyses were performed in R (R Core Team 2018) and an overview of the sequence/OTU number at each step of the pipeline is found in the Table S2 (Supporting Information).
A phylogenetic tree was built from the bioindicator OTU sequences as well as closely related sequences retrieved from NCBI GenBank in order to better assess their taxonomy. The closely related sequences were retrieved by aligning (BLASTn) the bioindicator sequences against the NCBI nucleotide database and choosing the two highest scoring matches. In addition, a set of cultivated gammaproteobacterial MOB sequences was retrieved in addition to a set of pmoA sequences belonging to upland-soil cluster (USC)-gamma that served as an outgroup. Sequences were aligned in MEGA7 (Kumar, Stecher and Tamura 2016) using MUSCLE, choosing the UPGMB clustering (Edgar 2004). The length of the alignment was inspected visually for an overlap for all sequences and a section of 440 bp was chosen for phylogenetic analysis. A phylogenetic tree was constructed in MEGA7 using the neighbor-joining method with the Jukes-Cantor correction and 500 bootstraps (Kumar, Stecher and Tamura 2016

Soil parameters
Soil temperatures decreased with depth in both grazed and exclosed plots, and higher temperatures were measured in the summer seasons than in the spring season (Table S3, Supporting Information). At the soil surface, temperatures up to 16 • C were observed but temperatures varied substantially depending on air temperature and cloud cover (Fig. S1, Supporting Information). Below the surface, temperatures rarely exceeded 8 • C throughout the peat profile. Slightly warmer temperatures were recorded in grazed plots in the top 10 cm of the peat soil.
The decrease in O 2 concentration with depth was similar in grazed (-0.51 ± 0.18 mg/L per cm depth) and exclosed plots (-0.35 ± 0.25 mg/L per cm depth). However, O 2 concentrations in grazed plots dropped from 9.8-11.5 mg/L O 2 at the surface to 1.7-9.5 mg/L O 2 at 5 cm depth. No drop was observed in exclosed plots when comparing surface concentrations (10.4-11.6 mg/L O 2 ) to 5 cm depth (9.6-12.1 mg/L O 2 ) and a more gradual decrease in O 2 concentration was observed (Fig. S2, Supporting Information).
Comparing the vegetation and the top 2 cm of peat soil, the water content was lower in exclosed plots (73.4-89.6 wt% H 2 O) than in grazed plots (88.7-94.7 wt% H 2 O) (Fig. 2), whereas between 2 and 10 cm below vegetation the water content was more similar for both environments. Overall, the soil water content measured in exclosed plots was 2%-15% lower than in grazed plots. SOM was slightly higher in exclosed peat (11.5 ± 3.2%) compared to grazed peat (8.3% ± 1.5%).
The in situ pore water CH 4 concentrations were higher at 10 cm depth than 5 cm depth in the grazed plots. Similarly, the CH 4 concentrations were higher at 20 cm depth than 15 cm depth in exclosed plots. Moreover, in situ CH 4 pore water concentrations were consistently higher in grazed plots than exclosed plots (Fig. S3, Supporting Information).

Potential CH 4 oxidation
Microcosm experiments were conducted ex situ to estimate the potential soil CH 4 oxidation rates at different depths in grazed and exclosed plots, for different seasons (spring and summer) and years. The highest CH 4 oxidation rates were measured at 0.5-2.5 cm depth in the grazed plots (115.0-319.6 μg CH 4 oxidized per g dry soil and day, Fig. 3). The exclosed plots had highest CH 4 oxidation rates at 3-8 cm depth (21.8-105.7 μg CH 4 oxidized per g dry soil and day, Fig. 3). This shift in potential CH 4 oxidation rates between the grazed and exclosed plots coincided with the shifts in O 2 concentrations, water content and CH 4 pore water concentrations. Overall higher CH 4 oxidation rates were measured in grazed plots, exceeding 50 μg CH 4 oxidized per g dry soil and day at most depths. In exclosed plots, CH 4 oxidation rates higher than 50 μg per g dry soil and day were almost exclusively observed in the zones of maximal CH 4 oxidation between 3 to 8 cm. The differences between grazed and exclosed plots, and different depths were true for both summer seasons (2015 and 2016) and the spring season. However, the potential CH 4 oxidation rates in spring were overall lower than in summer for the grazed plots, while for the exclosed plots spring and summer CH 4 oxidation rates were similar.

Bacterial and MOB community structure
We then wanted to identify the main MOB taxa within the bacterial communities to specifically target the MOB responsible for the CH 4 oxidation activity.
Larger amounts of DNA and RNA per gram dry soil were extracted from grazed plots compared to exclosed plots, suggesting a larger bacterial biomass in grazed soils (Fig. S4, Supporting Information). Sequencing of 16S rRNA gene libraries from these soils provided us with 10 816 sequences per library on average after quality filtering, the smallest library containing 2383 and the largest 19 608 sequences.
The results of the RDA showed that the bacterial communities in grazed plots differed significantly from the communities in the exclosed plots (P < 0.001, Fig. 4). The RDA showed that the sampling date had an impact on the communities in the grazed plots (P = 0.004), which was less pronounced for exclosed plots (P = 0.124), similar as observed for the measured CH 4 oxidation potentials.
The separation between grazed and exclosed plots correlated with ex situ CH 4 oxidation rates and the communities in the grazed plots were associated with high CH 4 oxidation rates while communities in the exclosed plots were associated with low rates (Fig. 4). However, CH 4 oxidation rates did not have a significant impact on the community structure (P = 0.300 grazed plots, P = 0.673 exclosed plots, P = 0.613 both treatments). All pvalues for the variables and variables' interaction tested in the RDA analyses are listed in Table S4 (Supporting Information).
The 16S rRNA gene sequences assigned to the order Methylococcales were relatively more abundant (Kruskal-Wallis rank sum test P < 0.001) in grazed plots than in the exclosed plots, with a relative abundance of 7.0% in grazed plots compared to below 1% in exclosed plots (Fig. S5, Supporting Information). OTUs assigned to Crenothrix and Methylobacter had higher relative abundances than other genera within Methylococcales, representing 22 out of 25 OTUs of that order and from 56% to 100% of the sequences (Fig. S7, Supporting Information). Both genera were relatively more abundant in grazed plots (Kruskal-Wallis rank sum test: P < 0.05 for Crenothrix and for Methylobacter P < 0.01). From the 8 bioindicator OTUs for the grazed plots, one Methylobacter OTU (X49) was identified as bioindicator (Fig. 4,  Fig. S6, Supporting Information). Among 13 OTUs identified as bioindicators for the exclosed plots, none of them belonged to the MOB.
To obtain further insights into the active MOB community, we sequenced pmoA transcript cDNA libraries from the summer 2015 microcosms and the spring and summer 2016 in situ soil samples using the two different pmoA primer pairs (Table S1, Supporting Information). The RDA analyses gave similar overall trends for both datasets. Therefore, the results from the mb661R pmoA dataset are used as the primary data basis for analyses, while the A682R pmoA dataset is used as a reference point to discuss uncertainties arising due to primer pair selection. Sequencing of pmoA gene libraries using the mb661R primer provided us with 29 149 sequences per library on average after quality filtering, the smallest library containing 9007 and the largest 58 612 sequences, whereas for the A682R primer an average of 22 340 sequences per library was provided, the smallest library containing 2213 and the largest library containing 53 950 sequences.
MOB community pmoA transcription in the grazed plots differed significantly from the exclosed plots (P < 0.001) (Fig. 5, Fig.  S8, Table S4, Supporting Information), following the differences in CH 4 oxidation rates. Sampling date also had a clear impact on the MOB pmoA expression in the grazed plots (P < 0.001), but not in the exclosed plots (P = 0.467).
The majority of pmoA transcripts belonged to the genus Methylobacter (Figs S9 and S10, Supporting Information). Furthermore, nearly all bioindicator OTUs (for grazed or exclosed plots) belonged to Methylobacter (Fig. 6). This indicates that a consortium of closely related species and strains within the same genus are primarily responsible for most of the CH 4 oxidation but are also very responsive to ecosystem change.
Methylomicrobium was the second most active genus based on the mb661R pmoA dataset (10.7% of the sequences in grazed plots, 27.6% in exclosed plots, Fig. S9, Supporting Information). OTU Methylomicrobium-M1 was the OTU with the highest overall abundance. However, the transcriptional activity of this and other Methylomicrobium OTUs were similar in all plots (Fig. 6)  Figure 2. Soil water content in spring (left) and summer 2015 and 2016 (right), comparing grazed treatment (blue) and exclosed treatment (green). The water content was measured for the vegetation (>0 cm soil depth), at the soil/vegetation interface (0 cm) and until a soil depth of 20 cm (y-axis). Each point represents one measurement. Soil water content (x-axis) varied from 73 to 95 wt%. Soil depths were chosen in order to include visually distinguishable layers as well as many depths within the layers suspected to account for the majority of CH4 oxidation (0-10 cm soil depth). . Potential CH4 oxidation (μg CH4 oxidized per g dry soil and per day) along vertical soils gradients for the grazed (two top figures) and exclosed treatments (two bottom figures). Filled symbols represent summer and open symbols represent spring. Each point represents one measurement. Oxidation rates from site SV1 and SV2 are shown on the left; and right-hand side respectively. The shaded area highlights the zone of maximum CH4 oxidation activity. CH4 oxidation measured above ground (i.e. vegetation) are > 0 on the y-axis, whereas below ground activity are < 0 on the y-axis. excluding those OTUs as bioindicator for grazed or exclosed plots.
MOB transcriptional profile based on the A682R pmoA dataset was slightly different from the mb661R pmoA dataset. The major discrepancy was the large amount of unidentified MOB annotated as MOB-like (Fig. S10, Supporting Information). OTU A6 had the highest relative abundance within the MOB-like group with no significant differences between the grazed and the exclosed plots, ranking fourth in relative abundance behind Methylobacter OTUs A1, A3 and A4.
Phylogenetic analysis of the pmoA sequences of the bioindicator OTUs showed that most of them cluster within Methylobacter, in most cases closer to uncultivated environmental sequences than cultivated strains (Fig. 7). Interestingly, the bioindicators were all members of distinct clusters showing that these are phylogenetically different MOB strains.

Different ecosystem states change the potential for CH 4 oxidation
In our study, we investigated how the presence or absence of herbivory affected the potential for CH 4 oxidation and the methanotroph community in a high-Arctic peatland. Herbivore exclusion had promoted a higher proportion of vascular plants (Fig. 1) and less dense soil structure, reflected in higher O 2 concentrations, lower water content and higher soil temperatures (Fig. 2, Table S3, Figs S1 and S2, Supporting Information). The higher temperatures may be explained by better insulation being provided by the thicker vascular plant cover (Sjögersten, Van Der Wal and Woodin 2008;Sjögersten et al. 2011;Falk et al. 2015). In addition, visual observations of living roots in the exclosed plots but not in the grazed plots confirmed previous observations of higher root and vascular plant biomass in the exclosed plots (Sjögersten et al. 2011). Lower in situ CH 4 concentrations in the exclosed plots (Fig. S3, Supporting Information) contrast the  Black lines indicate CH4 oxidation potential (μg CH4 oxidized per g soil and day). Black dots show the distribution of non-bioindicator OTUs while green dots represent bioindicator OTUs for exclosed treatment and blue dots represent bioindicator OTUs for grazed treatment. Bioindicator identities are represented by the letter M followed by a number, marking them as OTUs from the mb661R pmoA dataset. Taxonomic information about the bioindicator OTUs is found in the heatmap in Fig. 6. higher temperatures measured, as one would expect increased microbial activity at higher temperatures. However, the higher O 2 concentrations at 0-5 cm depth in the exclosed plots would promote CH 4 oxidation and inhibit CH 4 production, in line with our observations. We did not observe any seasonally dependent differences in water content in grazed plots. Exclosed plots had overall lower water contents than the grazed plots and also slightly higher water contents in spring compared to summer, possibly due to recent snowmelt (Fig. 2). In the lowest section we show the MOB OTUs with the highest relative abundance until representing 90% of the community. OTU names consist of the letter M plus a number, marking them as OTUs from the mb661R pmoA dataset. The color represents the relative abundance of a given OTU in a given sample.
The higher water content, higher in situ CH 4 concentrations and lower O 2 concentrations measured in the grazed plots were indicative of higher rates of CH 4 production in these soils (Table  S3, Fig. 2, Figs S2 and S3, Supporting Information). However, due to the higher SOM content available for microbial degradation in exclosed plots it cannot be excluded that the amount of CH 4 produced in exclosed plots occasionally can surpass the CH 4 produced in grazed plots.
The potential CH 4 oxidation rates were highest in the grazed plots ( Fig. 3) Furthermore, in these plots the zones of CH 4 oxidation were closer to the peat surface in grazed plots. In contrast to this, the lower in situ CH 4 concentrations and higher O 2 concentrations in the exclosed plots corresponded to a vertical shift of the maximum CH 4 oxidation zone from directly below the surface to between three and eight centimeters depth (Fig. 3). This matches the higher potential CH 4 oxidation rates measured in Figure 7. Neighbour-joining tree showing the phylogeny of the mb661R pmoA bioindicator OTUs (exclosed treatment in green, grazed treatment in blue), cultivated MOB strains (bold and italic) and related environmental sequences retrieved from Genbank (NCBI). Sequences belonging to the upland soil cluster gamma are used as outgroup to root the tree (shaded in red). Calculation was based on a 440-nucleotide alignment, using Jukes Cantor correction and 500 bootstraps. Bootstrap support is shown as node color ranging from blue (8%, lowest) to red (100%, highest). The length of the branches is based on the scale of 0.1 changes per nucleotide. grazed areas of alpine meadows (Abell et al. 2009) and smaller CH 4 net-emissions measured in ungrazed areas of the Zackenberg valley (Greenland) and Yukon-Kuskokwim Delta (Western Alaska) (Falk et al. 2015;Kelsey et al. 2016). A possible explanation for the higher potential CH 4 oxidation in the grazed sites is differences in nitrogen (N) availability. Ammonia (NH 4 ) concentrations has been shown to correlate with higher CH 4 oxidation rates and type I MOB abundances in rice paddy soils (Bodelier and Laanbroek 2004). Sjögersten et al. (2011) also showed higher N in grazed plots than in exclosed plots which can explain the higher CH 4 oxidation observed in grazed plots in our study. Interestingly, it has been proposed that N fertilization favors a lower diversity (genus level) in rice paddy soils (Noll, Frenzel and Conrad 2008). As such, we would expect to observe higher methanotroph diversities in exclosed plots than grazed plots, but we did not.

Different bacterial and methanotroph communities in grazed and exclosed soils
Related to the higher potential CH 4 oxidation rates, we observed a considerably more transcriptionally active methanotroph community in grazed than exclosed plots (Fig. S6, Supporting Information). This difference was emphasized by the overall higher DNA and RNA content per gram dry soil in the zone of maximal CH 4 oxidation in grazed peat soils compared to exclosed peat soils (Fig. S4, Supporting Information). Furthermore, the higher relative abundances of methanotrophs in the grazed plots corresponded with higher CH 4 oxidation rates measured in the microcosm experiment ex situ (Fig. 3). Similarly, a link between CH 4 oxidation rates and transcript abundances was previously demonstrated (Reim et al. 2012;Siljanen et al. 2012) but we did not apply RT-qPCR and cannot directly compare this.
Methylobacter made up the majority of the methanotroph communities at Solvatn. From the genomes of several Methylobacter species, we know that these microorganisms oxidize CH 4 using the particulate methane monooxygenase. Our sequencing efforts targeting pmoA transcripts confirmed this, as the majority of pmoA transcripts were assigned to Methylobacter ( Fig. 6 and Fig. S11, Supporting Information). Furthermore, we observed that a set of Methylobacter bioindicator OTUs were consistently more active in the maximal CH 4 oxidation zone of the exclosed plots while other OTUs were more active in the grazed plots, indicating that the different CH 4 and O 2 concentrations favor different Methylobacter OTUs. Similiarly, in stratified lakes the MOB communities were structured according to CH 4 and O 2 concentrations, providing for a niche-adapted community responsible for CH 4 oxidation dynamics (Mayr et al. 2020). An earlier microcosm study also supported the idea that closely related Methylobacter populations are adapted to different niches as they responded differently to O 2 tension (Oshkin et al. 2015).
CH 4 concentrations in Solvatn peat soil are high (Fig. S3, Supporting Information) while net net CH 4 emissions are low (Høj, Olsen and Torsvik 2005;Sjögersten et al. 2011). It has previously been suggested that such niche partitioning increases the exploitation of resources (Finke and Snyder 2008;Mayr et al. 2020). Thus, niche partitioning of closely related Methylobacter OTUs may explain the efficiency of CH 4 consumption in both grazed and exclosed peat soils at Solvatn.
Our study shows that phylogenetically distinct Methylobacter OTUs might find their ecological niches within micro niches of the same ecosystem as the most active fraction of the MOB community consisted of several closely related transcriptionally active Methylobacter populations (Figs. 6 and 7). Similar observations were reported from Lake Washington, Lake Pavin and the Canadian high Arctic (Costello and Lidstrom 1999;Martineau, Whyte and Greer 2010;Biderre-Petit et al. 2011), suggesting that our findings reflect a common occurrence. The bioindicator approach allows us to identify OTUs that respond to specific environmental changes in different ecosystems. By correlating past and future datasets this approach can help determining whether certain strains or species have the same roles and responses in other ecosystems or under other conditions.
It remains difficult to a draw a line between species and strains based on sequencing the pmoA genes or transcripts even though similarity cut-offs have been suggested for pmoA OTUs (Wen, Yang and Liebner 2016). A genome-based study revealed that a large variety of Methylobacter genomes which were earlier assigned as strains of M. tundripaludum SV96 are actually different species (Orata et al. 2018). Thus, some of the pmoA OTUs we have identified as bioindicators may be representative of different Methylobacter species, and so the OTU dynamics described here are in part reflecting the ecology of Methylobacter species.

CONCLUSION
Herbivory in Svalbard leads to reduced vascular plant and root biomass in peatlands, resulting in increased soil water content, higher in situ pore water CH 4 concentrations and reduced O 2 concentrations. These changes correspond with a shallower and more potent zone of maximal CH 4 oxidation in grazed peat compared to peat protected from grazing. Furthermore, the shallower CH 4 oxidation zone in grazed peat has a relatively more abundant and different MOB community than the exclosed peat, the major difference being the dominance of different Methylobacter OTUs. Nevertheless, Methylobacter comprise the major CH 4 filter in both peat soils, actively reducing the amount of CH 4 emitted to the atmosphere. This study emphasizes how herbivory leads to altered soil conditions that selects for different active MOB communities able to respond to increased CH 4 concentrations.

SUPPLEMENTARY DATA
Supplementary data are available at FEMSEC online.

ACKNOWLEDGMENTS
The funding for this study was provided by NORRUSS (Grant: 233645/H30) and Svalbard Science Forum (AFG Grant: 246113/E10 and AFG Grant: 256933/E10) from the Research Council of Norway. AT