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Departamento de Ciencias Forestales, Universidad Nacional de Colombia Sede Medellín, Medellín, ColombiaAlvaro Duque, Miguel A. Peña & Sebastián González-CaroGrupo de Investigación en Biodiversidad, Medio Ambiente y Salud -BIOMAS – Universidad de Las Américas (UDLA), Quito, EcuadorFrancisco Cuesta, Marco Calderón-Loor & Esteban PintoDepartment of Plant and Microbial Biology, University of Minnesota, Saint Paul, MN, USAPeter KennedySchool of Geography, University of Leeds, Leeds, UKOliver L. PhillipsCentre for Integrative Ecology, School of Life and Environmental Sciences, Deakin University, Melbourne, VIC, AustraliaMarco Calderón-LoorInstituto de Ecología Regional (IER), Universidad Nacional de Tucumán (UNT) – Consejo Nacional de Investigaciones Científicas y Técnicas (CONICET), Tucumán, ArgentinaCecilia Blundo, Julieta Carilla, Ricardo Grau, Agustina Malizia & Oriana Osinaga-AcostaHerbario Nacional de Bolivia (LPB), La Paz, BoliviaLeslie Cayola, Alfredo Fuentes & María I. Loza-RiveraMissouri Botanical Garden, St. Louis, MO, USALeslie Cayola, Alfredo Fuentes & María I. Loza-RiveraCenter for Conservation and Sustainable Development, Missouri Botanical Garden, St. Louis, MO, USAWilliam Farfán-Ríos, María I. Loza-Rivera & J. Sebastián TelloLiving Earth Collaborative, Washington University in Saint Louis, St. Louis, MO, USAWilliam Farfán-RíosPlant Ecology and Ecosystems Research, University of Gottingen, Gottingen, GermanyJürgen HomeierCentre of Biodiversity and Sustainable Land Use (CBL), University of Gottingen, Gottingen, GermanyJürgen HomeierEnvironmental Change Institute, School of Geography and the Environment, University of Oxford, Oxford, UKYadvinder MalhiFacultad de Ciencias Agrarias, Universidad Nacional de Jujuy, Jujuy, ArgentinaLucio MaliziaUniversité du Quebec a Montreal, Montreal, QC, CanadaJohanna A. Martínez-VillaDepartment of Biology, Washington University in St. Louis, St. Louis, MO, USAJonathan A. MyersConsorcio para el Desarrollo Sostenible de la Ecorregión Andina (CONDESAN), Quito, EcuadorManuel PeralvoColumbus State University, University System of Georgia, Columbus, GA, USAEsteban PintoCarbon Cycle and Ecosystems, Jet Propulsion Laboratory, California Institute of Technology, Pasadena, CA, USASassan SaatchiCenter for Energy, Environment and Sustainability, Winston-Salem, NC, USAMiles SilmanCentro Jambatú de Investigación y Conservación de Anfibios, Quito, EcuadorAndrea Terán-ValdezBiology Department, University of Miami, Coral Gables, FL, USAKenneth J. Feeley More

Tractable systemsTractable systems are models typically of known and reduced complexity that can be operationalized and reproduced over relatively short periods of time. To formalize our study using tractable systems, we consider a (regional) pool ({mathcal{R}} =left{1,2,cdots ,Sright}) of (S) resident species and one non-resident species denoted by “(I)” (Fig. 1A). We denote the resident community by ({mathcal{M}} subseteq {mathcal{R}}), which is the species collection that coexists obtained by assembling all resident species simultaneously. Additionally, let ({ {mathcal{M}} }_{p}) denote the perturbed community formed by the species collection that coexists when assembling all residents and the non-resident species simultaneously assuming the possibility of multiple introductions. Note that this mechanism corresponds to a top-down assembly process.33 Then, the non-resident species is classified as a game-changing species if it changes the number of resident species that coexist: (|{ {mathcal{M}} }_{p}{I}|,ne, | {mathcal{M}} |). Figure 1A illustrates the concept of a game-changing species in a hypothetical microbial community of (S=2) resident species. Here, one possible context for the resident species is that one species excludes the other, e.g., ({mathcal{M}} ={1}) (Fig. 1B). In this case, the non-resident species is a game-changing species if it promotes the establishment of the other resident (Fig. 1C). Note that we do not consider a change when eliminating the current resident species. The other context for the resident species is that both coexist ({mathcal{M}} ={1,2}) (Fig. 1D). In this case, a non-resident species is a game-changing species if it suppresses the establishment of at least one of the residents, e.g., ({ {mathcal{M}} }_{p}={1,I}) (Fig. 1E). Note that a game-changing species can be either colonizer or transient depending on the dynamics.Fig. 1: Game-changing species for a resident microbial community.Illustration of different contexts leading to game-changing and non-game-changing species. Panel A shows a hypothetical microbial community with a pool ({mathcal{R}} ={1,2}) of two resident species (pink and yellow) and one non-resident species “(I)” (green). Panel B shows the context when one species excludes the other, the resident community contains a single resident (({mathcal{M}} ={1})). To change the resident community, the non-resident species needs to promote the establishment of the other species (in this case yellow, but the example can also be done for the pink species). Panel C provides examples of game-changing and non-game-changing non-resident species for the example presented in Panel B (as the outcomes of the perturbed communities ({ {mathcal{M}} }_{p})). Panel D shows another context when the two resident species coexist (({mathcal{M}} ={1,2})). To change the resident community, the non-resident species needs to suppress the establishment of any of the species (green or yellow). Panel E provides potential outcomes of perturbed communities of game-changing and non-game-changing non-resident species for the example presented in Panel D. In this context, the change happens by suppressing the yellow species (the same can be said for the pink species). Note that in all contexts, the non-resident species can be either a colonizer (can become established in the perturbed community) or transient (cannot colonize).Full size imageWe study the generalization of game-changing species under controlled conditions using in vitro experimental soil communities and under changing conditions using in vivo gut microbial communities (see SI for details about these experimental systems). Note that in vitro experiments usually create ad hoc conditions for species by putting them outside of their natural changing habitats, assuring that species survive in monocultures, and by forming interspecific interactions that may not occur otherwise. Instead, in vivo experiments are performed within living systems, resembling much closer the natural habitat of species and their interspecific interactions. Both types of systems are of reduced complexity, allowing the monitoring and reproducibility of experiments. The studied in vitro soil communities are formed by experimental trials of eight interacting heterotrophic soil-dwelling microbes:30 Enterobacter aerogenes, Pseudomonas aurantiaca, Pseudomonas chlororaphis, Pseudomonas citronellolis, Pseudomonas fluorescens, Pseudomonas putida, Pseudomonas veronii, and Serratia marcescens. These experiments were performed by co-inoculating species at different growth–dilution cycles into fresh media. Each species was cultured in isolation. All experiments were carried out in duplicate. The studied in vivo gut communities are formed by experimental trails of five interacting microbes commonly found in the fruit fly Drosophila melanogoster gut microbiota:34 Lactobacillus plantarum, Lactobacillus brevis, Acetobacter pasteurianus, Acetobacter tropicalis, and Acetobacter orientalis. These experiments were performed by co-inoculating species through frequent ingestion in different flies. All experiments were replicated at least 45 times. These two data sets are, to our knowledge, the closest and best described systems of two- and three-species communities currently available describing species coexistence (not just presence/absence records) under two contrasting environmental conditions.Focusing on in vitro communities, we studied all 28 pairs and 56 trios formed by the eight soil species.30 This provided 168 cases, where it is possible to investigate the expected result (({ {mathcal{M}} }_{p})) of assembling a non-resident species together with a resident community (21 cases for each of the 8 studied microbes). The overall competition time was chosen such that species extinctions would have sufficient time to occur, while new mutants would typically not have time to arise and spread. Similarly for the in vivo communities, we studied all 10 pairs and 10 trios formed by the 5 gut species, which provided 30 cases equivalent to the soil experiments.34 Because species extinctions in in vivo communities are harder to establish, we classified as an expected extinction to any species whose relative abundance was less than 10% in at least 71% of all (47–49) replicates, which corresponds to less than 1% of cases under a binomial distribution with (p=0.5) (slightly different thresholds produce qualitatively similar results). Each of these 168 and 30 cases for soil and gut communities, respectively, represents a given resident community (({mathcal{M}})) formed by a pool of two resident species (({mathcal{R}} ={1,2}), ({mathcal{M}} subseteq {mathcal{R}})) where the target for a non-resident species ((I)) can be either to promote or to suppress the establishment of resident species (({mathcal{R}} {cup }left{Iright}), ({mathcal{M}}_{p} setminus {I},ne, {mathcal{M}})). Non-resident species that are expected to survive in ({ {mathcal{M}} }_{p}) are classified as colonizers; otherwise they are classified as transients.Empirical contextsTo investigate the role of context dependency in the game-changing capacity of microbial species, we study the extent to which a given species can be classified as a game-changer regardless of the resident community it interacts with or if it is the resident community that provides the opportunity for a non-resident species to be a game-changer. Specifically, for each species, we calculate the fraction of times such a species changes the resident community conditioned on the type (whether it is a colonizer or a transient) and target (whether promoting or suppressing). Then, we calculate the probability ((p) value) of observing a fraction greater than or equal to the observed fraction under the given type/target (using a one-sided binomial test with mean value given by the empirical frequency within each type/target). High (p) values (e.g., ( > 0.05)) would be indicative of the importance of context-dependency and not of the intrinsic capacity of species.Next, we quantify the average effect of empirical contexts shaping the game-changing capacity of non-resident species. Specifically, we measure the type’s average effect on changing the community using ({E}_{Y}=P(C=1|Y=1)-P(C=1|Y=0)). Here, (C=1) if the non-resident species was a game-changer ((C=0) if it was not), and where (Y=1) if the species was a colonizer ((Y=0) if the species was transient). The non-parametric quantity (P(C|Y)) corresponds to the frequency of observing (C) given (Y). Thus, ({E}_{Y} , > , 0) (resp. ({E}_{Y} , , 0) (resp. (,{E}_{T} , ,0)). Panel H shows that the non-resident species will be able to change the community based on structuralist theory.Full size imageTractable theoretical systems: structuralist theoryWhile mutual invasibility theory has provided key insights regarding population dynamics,29,30,35 it has been shown that it cannot be directly generalized to multispecies communities.37,38,39 Hence, as an alternative potential generalization, we introduce a second heuristic rule based on structuralist theory,32,40,41 Across many areas of biology, the structuralist view has provided a systematic and probabilistic platform for understanding the diversity that we observe in nature,31,42,43 In ecology, structuralist theory assumes that the probability of observing a community is based on the match between the internal constraints established by species interactions (treated as physico-chemical rules of design) within a community and the changing external conditions (treated as unknown conditions).32,44,45 This other premise has also been shown to be as successful as mutual invasibility in predicting the outcome of surviving species in the studied in vitro soil communities,32 but it has not been tested for its generality.Formally, the structuralist framework assumes that the per-capita growth rate of an (i)th species can be approximated by a general phenomenological function ({f}_{i}({N}_{1},cdots ,{N}_{S},{N}_{I};{boldsymbol{theta}})), i.e.,$$frac{d{N}_{i}}{dt}={N}_{i} {f}_{i}({N}_{1},cdots ,{N}_{S},{N}_{I};{mathbf{theta}}),qquad iin {mathcal{R}}{cup}{I}$$
(1)
Above, ({N}_{i}) represents the abundance (or biomass) of species (i). The functions ({f}_{i}) encode the internal constraints of the community dynamics.46 The vector parameter ({mathbf{theta}}) encodes the external (unknown) conditions acting on the community, which can change according to some probability distribution (p({mathbf{theta}})). For a particular value ({mathbf{theta}}={{mathbf{theta}}}^{ast }), a species collection ({mathscr{Z}}subseteq {mathcal{R}} {cup }{I}) is said feasible (potentially observable) for Eq. (1) if there exists equilibrium abundances ({N}_{i}^{ast } , > , 0) for all species (iin {mathscr{Z}}) and ({N}_{i}^{ast }=0) for (i,notin, {mathscr{Z}}) (i.e., ({f}_{i}({N}_{1}^{ast },cdots ,{N}_{S}^{ast },{N}_{I}^{ast };{{mathbf{theta}}}^{ast })=0) for all (i)).40 Then, we can use Eq. (1) to push-forward (p({mathbf{theta}})) and estimate the probability that a randomly chosen species (i) is feasible with ((iin {mathcal{R}} {cup }{I})) and without ((iin {mathcal{R}})) the non-resident species under isotropic changing conditions, respectively. In this form, the effect of a non-resident species (I) on a resident community can be characterized by the expected maximum impact on its feasibility, i.e., ({Delta }_{{{F}}}=p(i| {mathcal{R}} {cup }{I})-p(i| {mathcal{R}} )) (Fig. 2E–H).To make this framework tractable, we leverage on the mathematical properties of the linear Lotka–Volterra (LV) system47 with the per-capita growth rate ({f}_{i}({N}_{1},cdots ,{N}_{S},{N}_{I};{mathbf{theta}})=mathop{sum}limits_{jin {mathcal{R}} {cup }{I}}{a}_{ij}{N}_{j}+{theta}_{i}) for (iin {mathcal{R}} {cup }{I}). While the linear LV system can be interpreted under many different assumptions,47 we follow its most general interpretation as a first-order approximation to Eq. (1).46 In this system, the time-invariant community structure consists of the intraspecific and interspecific species interactions ({bf{A}}=({a}_{ij})in {{mathbb{R}}}^{(S+1)times (S+1)}), and the external factors ({mathbf{theta}}=({theta }_{1},cdots ,{theta }_{S},{theta }_{I})in {{mathbb{R}}}^{S+1}) consist of density-independent intrinsic per-capita growth rates of all species. We assume that (p({boldsymbol{theta }})) is uniform over the positive parameter space (conforming with ergodicity in dynamical systems32) and find analytically the external conditions compatible with the feasibility of a randomly chosen species within a given community ({bf{A}}), i.e., (p(i|{bf{A}})) (see SI). This framework is robust to changes in the system dynamics since (p(i|{bf{A}})) is identical for all systems that are topologically equivalent to the linear LV system32,48 and a lower bound for systems with higher-order terms.41 Note also that while higher-order interactions may impact the dynamics of microbial communities49,50, their incorporation into ecological models as higher-order polynomials rend intractable and super-sensitive systems (no closed-form solutions can be found in terms of radicals)41,51,52,53.To quantify the contribution to feasibility (({Delta }_{{rm{F}}})) of a non-resident species under the structuralist framework defined above, we infer both the resident interaction matrix ({bf{A}}) and the perturbed interaction matrix ({{bf{A}}}_{p}) using only information from experimental monocultures and pairwise cocultures. Interaction matrices were inferred by fitting the linear LV system using the different repetitions of the observed survival data (see SI and Fig. S1). To make the structuralist framework comparable with the mutual invasibility framework, we introduce a heuristic rule based on structuralist theory formalized in a binary variable (({{F}})) that when anticipating the promotion (resp. suppression) of resident species becomes ({{F}}=1) if ({Delta }_{{{F}}} , > , 0); otherwise ({{F}}=0) if ({Delta }_{{{F}}} , More

We successfully sequenced 16S rRNA gene amplicons from 454 samples with universal primers and 283 samples with archaea-specific primers, respectively (see Supplementary Table 2), and recovered 260,266 ASVs in the universal 16S rRNA gene dataset and 28,123 ASVs in the archaea-specific dataset (Supplementary Fig. 2). As samples from the Atacama Trench region included sectioning at higher depth resolution (HR sectioning scheme), we will present and discuss these first.Variability of microbial community composition along the Atacama Trench axisThe sediments of the Atacama Trench showed the shallowest oxygen penetrations found in any hadal trench to date, ranging from 4.1 cm at the southernmost site A6 to 3.1 cm at northernmost A10, and reflected a high organic carbon flux from the Humboldt upwelling system [22, 26]. Correspondingly, nitrate penetration depths ranged from 8 to only 6 cm with dissolved, ferrous iron accumulating below, while hydrogen sulfide was not detected (see Supplementary Fig. 1 and Supplementary Table 1).Comparison of the community structure obtained with universal primers within the Atacama Trench indicated very similar trends with sediment depth for all sites, with a gradual change from the sediment surface to deeper sediment horizons, and with only marginal overlap between individual redox zones (Fig. 2A). Similar patterns were observed using different dissimilarity metrics (Bray Curtis, weighted/unweighted UniFrac), ordination techniques (NMDS/t-SNE), and sectioning schemes (HR/CR; data not shown). The downcore gradient of microbial communities was also evident within individual redox zones. Thus, samples from the same sediment horizon (e.g., 1–2 cm) but from different sites, with geographic distances of up to 430 km, were more similar to each other than to their respective adjacent horizons, above (0–1 cm) or below (2–3 cm) (Supplementary Fig. 3A, B). The horizontal similarity was particularly pronounced in the upper part of the oxic zone, while it decreased toward the bottom of the nitrogenous zone and increased again in the ferruginous zone (Supplementary Fig. 3A, B). The CR sample subset contained triplicates from separate sediment cores originating from two multicorer deployments, and thus included two cores sampled within a distance of 0.1–1 m and one sampled at an estimated distance of 10–100 m from the other two. Triplicate samples from the same sediment horizon were more similar to each other (1 – Bray Curtis dissimilarity ~0.7–0.9) than to samples from the same horizons at other sites (~0.4–0.8; Supplementary Fig. 4A, C). This implies some increase of variability with geographic distance along the trench axis.Fig. 2: Microbial community composition in the Atacama Trench.Principal coordinate analysis (PCoA) of Bray Curtis dissimilarities between hadal samples from the Atacama Trench in the universal 16S rRNA gene (A) and archaea-specific 16S rRNA gene (B) data. The color gradient represents sediment depth and ovals mark the 95% confidence intervals of multivariate normal distributions of the oxic, nitrogenous, and ferruginous zones, respectively. Different symbols correspond to different sites. C Relative read abundance (%) on phylum/class level of the ten most abundant taxonomic groups (universal 16S rRNA gene data) grouped by redox zone and by depth within each zone in hadal samples from the Atacama Trench. Both the color gradient and the number within the squares indicate of the average relative read abundances within the respective sample group.Full size imageThe steep change in community composition with increasing sediment depth yet relatively high similarity of communities from the same sediment depth at different sites was unexpected. Indeed, we expected that the irregular depositional regime of hadal trenches [18, 21], which was indicated in all hadal sediment cores through color layering and by site-specific fluctuations in depth distributions of porosity, TOC content, and cell numbers [22], would leave an imprint in the community. A closer examination of depth trends at individual sites based on Bray Curtis dissimilarity occasionally revealed compositional fluctuations with depth that may be related to depositional events (Supplementary Fig. 5). For instance, at sites A3 and A4 the microbial communities in the oxic zone were more similar to those from the ferruginous zone at around 15–25 and 9–15 cm, respectively, than to the samples of the nitrogenous zone located in between them (Supplementary Fig. 5). This hinted that local depositional events might have entombed parts of the microbial community. We suggest that such events contributed to the enhanced site–site variability in the nitrogenous and ferruginous zones (Supplementary Fig. 4A, C).Compositional changes over sediment depth and redox zonation along the Atacama TrenchThe observed trends in beta diversity were reflected by distinct phylum-level changes that followed redox zonation and sediment depth (Fig. 2C and Supplementary Fig. 6). Conversely, subsurface peaks of microbial abundance [22] were not reflected in the relative abundance patterns of different phyla (Proteobacteria always split to class level yet referred to as phyla for simplicity), which changed steadily with increasing sediment depth. For instance, some of the dominant groups, Gammaproteobacteria (20.9%; mean read abundance per sediment depth), Bacteroidetes (17.1%), and Thaumarchaeota (12.4%), peaked in relative abundance in the oxic zone and then decreased. Alphaproteobacteria (13.7%) on average had the highest relative abundances in the nitrogenous zone and became rather rare in the ferruginous zone. Planctomycetes rose in relative abundance below the oxic zone from around 9 to 15% and remained at this level below. Atribacteria showed the largest change in relative abundance. After being close to detection limit with an average relative abundance of 0.004% in the oxic and nitrogenous zones, their relative abundance increased approximately ten-fold for every centimeter from the transition to the ferruginous zone, until they became the dominant phylum in deeper sediment sections. Aside from Atribacteria, other lineages such as “Candidatus (Ca.) Marinimicrobia” (0.1–4.6%), “Ca. Woesearchaeota” (1.3–11%) and “Ca. Patescibacteria” (0.7–4.7%) increased steadily with increasing sediment depth, while Acidobacteria (~3.4%) and Deltaproteobacteria (~6.1%) showed almost no change. As microbial abundance in the hadal samples of this study fluctuated within less than one order of magnitude with depth [22], these relative abundance patterns resembled absolute abundances estimated by normalizing the data to cell numbers (data not shown).The directional changes in the microbial community composition with sediment depth and associated redox zonation indicated an active community turnover. Similar succession patterns of Gammaproteobacteria, Thaumarchaeota, Planctomycetes and other major microbial taxa have been found in sediments across the entire oceanic depth range from less than a 100 m water depth to the bottom of the Challenger Deep in the Mariana Trench [9, 24, 25]. Our data indicate that some of these directional changes are associated with redox stratification and thus are an inherent characteristic of cohesive marine sediments.Assembly of subsurface phyla in the ferruginous zone in the Atacama TrenchThe high spatial resolution of sampling across redox zones at multiple sites provides new insight into the assembly of deeper microbial communities. For example, combining the relative read abundance of Atribacteria (Fig. 2C) with total cell counts [22] (ignoring potential PCR bias and assuming the same 16S rRNA gene copy numbers in this group as in the community on average), we estimate an absolute increase of Atribacteria from a mean of 5.4 × 103 cells cm−3 at the upper boundary of the ferruginous zone at 6 cm depth to 1.2 × 107 cell cm−3 at 30 cm sediment depth ( >2000-fold increase). Excluding mortality, this can be accomplished in 11 generations, and given an estimated sedimentation rate during periods with no mass depositions of approximately 0.05 cm year−1 (unpublished data) would have occurred over approximately 500 years. Although the number of generations is a minimum estimate, this timeframe appears to leave relatively little opportunity for diversification, as previously concluded for deeper subsurface sediments [11].We further note that bioturbation in hadal sediments is mostly limited to meiofaunal infauna and epibenthic amphipods; hence, sediment mixing is unlikely to affect the depth distribution of microbes below the topmost centimeters [38]. As discussed in previous studies, vertical dispersal of microbes by means of active motility is unlikely to play a role in community assembly in cohesive sediments due to energetic constraints and short-distance chemical gradients [9, 39]. As the sediment in both the Kermadec and in the Atacama trench is cohesive [26], and in accordance with previous studies in deeper redox zones [9, 10], we therefore conclude that selection is likely the dominant force controlling community composition and, e.g., giving Atribacteria their dominant role in the ferruginous zone. They appear to grow from a small seed stock that arrives at the sediment surface and survive burial in an inactive state, until oxygen and nitrate are depleted. Other obligate anaerobes in marine sediments may be subject to similar constraints (see also [10]). This implies that there is little diversification potential for obligate anaerobes in hadal trench sediments. Other anaerobic niches in the hadal zone that might have more diversification potential include hydrothermally active sites and the guts of fauna [40, 41]. However, the conditions in guts and hydrothermally active sediments differ from those of cold deep-sea sediments, and these environments therefore harbor very different microbial communities [42, 43]. Hence, the majority of obligate anaerobes must have originated from the overlying water column and come with the necessary adaptations for the increased hydrostatic pressure and other conditions in hadal sediments. We therefore hypothesize that most obligate anaerobes in hadal sediments tolerate but do not prefer hadal pressures.Frequency distribution of ASVs and taxonomic affiliation of cosmopolitans along the Atacama TrenchDespite the large number of ASVs present in our dataset, only few were found in all samples from a given redox zone, yet these cosmopolitans tended to account for a large fraction of sequencing reads (Supplementary Fig. 7). This was especially pronounced in the rarefied data from the oxic zone where 365 out of 24,844 ASVs occurred across all oxic samples and comprised over 40% of all reads obtained from this zone, thereby contributing substantially to the similarity between cores and sites within the Atacama Trench (Fig. 2). The majority of these ubiquitous reads originated from ASVs belonging Gammaproteobacteria, Thaumarchaeota, Alphaproteobacteria, and Bacteroidetes (Supplementary Fig. 8). The nitrogenous and ferruginous communities were generally more variable, but ubiquitous ASVs accounted for 15% and 10% of all reads, respectively. In both zones most of the reads originated from ASVs classified as Alphaproteobacteria and Bacteroidetes, with ubiquitous ASVs belonging to Ca. Phycisphaerae becoming more abundant in the ferruginous zone.OTUs with high abundances were previously found to be cosmopolitan in deep-sea sediments [6]. Here, we show that this observation does not change when using ASVs and thus a much finer phylogenetic resolution for the formation of ecological units. The decrease of cosmopolitan ASVs in the nitrogenous and ferruginous zones relative to the oxic zone might be due to dispersal barriers in combination with the small seed-stocks of anaerobes in the upper parts of the sediment, which may lead to a higher level of stochasticity in community assembly in deeper sections. In the oxic zone, physical disturbances lead to resuspension of sediment particles and microbes into the water column [44], where they can be transported along trench axes by bottom currents known to ventilate trenches [45]. Therefore, we suggest that dispersal resulted in greater relative read abundances of ubiquitous ASVs in the oxic zone than in the nitrogenous and ferruginous zones.Core microbiomes of each redox zone along the Atacama TrenchTo further analyze the overlaps between abundant community members across redox zones, we performed a core community analysis using the toolset of the ampvis2 R package with adjusted cutoff parameters [32] (see Supplementary Material and Methods). This analysis defines ASVs as part of the core microbiome, when they are above 0.05% relative abundance and within the top 50% of all reads. This classified more than 99% of all ASVs as rare biosphere, while the remaining 441 core ASVs accounted for almost half of all reads (Supplementary Fig. 9A). Each redox zone had a distinct core microbiome, with 196, 66, and 91 core ASVs in the oxic, nitrogenous, and ferruginous zones, respectively, comprising 10.6%, 4.6%, and 8.5% of all reads. The three zones had 17 core ASVs in common that comprised 8.2% of all reads. Aside from these common ASVs, the overlaps between the core microbiomes of the oxic and nitrogenous redox zones were greater than those with the ferruginous zone, with the oxic and nitrogenous sharing an additional 60 ASVs (10.3% of all reads). By contrast, the oxic and nitrogenous zones only shared additional 3 (0.4% of all reads) and 8 (1.5% of all reads) ASVs with the ferruginous zone, respectively. Members of the core microbiome are usually abundant species that are present not merely due to immigration or advection but also through growth, and that are of biogeochemical importance [46, 47]. As the phylum-level composition of the core microbiome in each redox zone was mostly congruent with the overall relative abundance of phyla in each zone (Supplementary Fig. 9B), the distinct shifts in the core microbiome compositions between the zones hint at the potential niche spectra of individual phyla associated with each redox zone (see Supplementary Fig. 9). While many of the core ASVs seemed to thrive in both the oxic and in the nitrogenous zone, the conditions of microbial life seemed to change relatively abruptly when entering the ferruginous zone, resulting in the recruitment of deep-biosphere taxa.Community composition of Archaea along the Atacama TrenchAround 20% of all ASVs in the universal 16S rRNA gene dataset were classified as Archaea. However, due to known mismatches of universal 16S rRNA gene primer sets with archaeal lineages, in particular the phylum Thaumarchaeota, we thus also sequenced archaea-specific 16S rRNA gene amplicons with the same read depth. This primer set recovered approximately three times more thaumarcheotal ASVs than the universal set (4410 vs 1477) and also showed a better coverage over Euryarchaeota (3728 vs 2032), Crenarchaeota (1884 vs 707, including “Ca. Bathyarchaeia”), “Ca. Hydrothermarchaeota” (313 vs 101), and Hadesarchaea (71 vs 26). By contrast, the universal 16S rRNA gene dataset contained 17 times more “Ca. Woesearchaeota” ASVs (42,582 vs 2512), with this phylum even dominating ASV richness over Thaumarchaeota in the universal dataset. Sequencing the HR horizons with this primer set was only successful for only a small number of the samples. As CR horizons were more successful, we focus on this dataset.Thaumarchaeota was the overwhelmingly dominant phylum in the archaeal dataset and drove most of the dissimilarity between individual redox zones (Fig. 2B). In the oxic and nitrogenous zones, they contributed up to 99.3% relative abundance, and other lineages, particularly Crenarchaeota, “Ca. Hydrothermarchaeota,” Euryarchaeota, and “Ca. Asgardaeota,” only increased in relative abundance in the ferruginous zone (Supplementary Fig. 10). Consequently, ordination plots of this dataset only showed a depth gradient to the bottom of the nitrogenous zone, while samples from the ferruginous zone deviated strongly from this gradient (Fig. 2B). Estimates of absolute abundances of the individual archaeal phyla from the universal 16S rRNA gene dataset (Supplementary Fig. 11) showed that the relative depth-wise increase of “Ca. Asgardaeota” (0–9.8%) and Crenarchaeota (0–32.9%) in the archaeal dataset reflects their increase in absolute abundance from 1.4 × 103 to 3.4 × 105 “Ca. Asgardaeota” per ml sediment and 3.7 × 102 to 4.4 × 105 Crenarchaeota per ml sediment. This suggested possible growth of these lineages in hadal sediments.Globally, bacterial lineages dominate over archaeal lineages in marine water columns and surface sediments [48, 49]. The only archaeal phylum in these habitats of comparable abundance is Thaumarchaeota. However, in coastal subsurface sediments, archaeal lineages belonging to “Ca. Lokiarchaeota” and the Miscellaneous Crenarchaeota Group (here referred to as “Ca. Bathyarchaeia”) were found to comprise the majority of intact microbial cells, and Archaea in general contributed significantly to the carbon turnover in these systems [49,50,51,52]. These studies showed that recruitment of archaeal strains occurs in the first few centimeters of these sediments but did not provide a more specific location or connection to biogeochemistry. Our data indicated that the enrichment of Crenarchaeota (including “Ca. Bathyarchaeia”) and “Ca. Asgardaeota” started similarly to that of Atribacteria at the interface of the nitrogenous and ferruginous zones, and was accompanied by an increase in archaeal abundance relative to bacteria. Consequently, both the universal and the archaeal 16S rRNA gene data suggested that the interface between the nitrogenous and ferruginous zones marks the beginning of assembly of subsurface-like microbial communities. This interface also marks the transition from nitrate reduction to iron and/or sulfate reduction as the dominant terminal electron accepting processes. According to existing models, this transition is further associated with a switch in how organic matter is mineralized, with aerobes and denitrifiers being capable of degrading and oxidizing complex organic substrates individually, while a functional division between fermentation and respiration among two sets of organisms is necessary during dissimilatory iron and sulfate reduction [53, 54]. Therefore, we suggest that the distinct differences in microbial communities across the nitrogenous-ferruginous interface are due to the utilization of different electron acceptors and the associated division of labor that causes a rise of fermenters.Community composition across hadal, abyssal, and bathyal sedimentsTo get further insights to factors influencing microbial community composition in hadal sediments, we compared the Atacama Trench to the Kermadec Trench in the less productive western South Pacific, as well as to abyssal and bathyal sites adjacent to these trenches. Kermadec Trench sediments were characterized by deeper oxygen and nitrate penetration depths than in the Atacama Trench (8.5 to >18 cm and 15 to >30 cm, respectively), pushing the ferruginous zone below the sampled sediment horizons at one of the sites (K4 [26], Supplementary Table 1). Consequently, data on the ferruginous zone of the Kermadec Trench were scarce (Supplementary Table 1). In addition, the entire oxic zone was only covered with confidence at site K6, due to potential loss of surface layers at the other stations. Similar to the Atacama Trench, a non-steady state depositional regime in the Kermadec Trench was indicated by fluctuating microbial abundances and visible layering of the sediments.Sediments from the abyssal plains adjacent to both trenches (A7 and K7) showed even deeper oxygen penetration beyond the measured range of the oxygen profiling lander ( >20 cm) and projections indicated that these sediments were oxic across the entire interval analyzed here [26]. In contrast to the trench sites, microbial abundance decayed exponentially with sediment depth and was associated with parallel decreases in TOC content [22]. Conversely, sediment cores from the bathyal (A1) and abyssal (A9) continental slope sites next to the Atacama Trench reached into ferruginous and nitrogenous horizons, respectively, with oxygen penetrating to 1.9 and 6.7 cm, respectively, and nitrate reaching ~6.5 cm at A9. The TOC and microbial abundances showed no clear downcore pattern at these sites [22].At the phylum level, the hadal communities revealed by universal primers were similar in the two trenches, though the drop in Thaumarchaeota abundance was more sharply located at the oxic-nitrogenous interface in the Kermadec Trench than in the Atacama Trench (Fig. 3A and Supplementary Fig. 12A). The Kermadec Trench also exhibited higher relative abundances of “Ca. Woesearchaeota” (18.2% vs 9.2%) in deeper sediment horizons. The archaeal datasets differed more clearly between the two trenches (Supplementary Fig. 12B). While Crenarchaeota reached almost 20% abundance in the Atacama Trench and were detected in the oxic zone, they were essentially absent in the Kermadec Trench. In contrast, “Ca. Diapherotrites” (DPANN) contributed up to 28.6% of relative abundance in the deeper sections of the Kermadec sediments but were almost absent in the Atacama Trench. Similar small-scale differences in the relative abundances of microbial phyla were previously observed between the Japan, Izu-Ogasawara and Mariana trenches [24], Mariana and Mussau trenches [55], as well as between the Mariana and Kermadec trenches [25]. Peoples et al. [25] showed that the Kermadec Trench was enriched in Bacteroidetes, “Ca. Hydrogenedentes” and Planctomycetes in comparison to the Mariana Trench, while the latter had higher relative abundances of “Ca. Marinimicrobia,” Thaumarchaeota, “Ca. Woesearchaeota,” and Chloroflexi. Along with this high similarity between trenches on the phylum level, 58% of all OTUs with ≥97% sequence similarity were shared between the Mariana and Kermadec trenches and these shared OTUs comprised over 95% of all 16S rRNA gene amplicon reads [25]. Thus, they concluded that endemism did not cause the community dissimilarity between the trenches and did not occur on the OTU level. Our ASV-based analysis provided a finer phylogenetic resolution [30], had approximately ten-fold higher sequencing depth, and spanned over three redox zones (up to 40 cm sediment depth) instead of the first 10 cm as in the previous study. A core-to-core comparison from A6 and K6 (the only site with an undisturbed sediment surface in the Kermadec Trench), similar to that of Peoples et al. [25], revealed that the sites shared around 8% of all ASVs, yet these shared ASVs accounted for 62% of all obtained reads from the respective samples. A core microbiome analysis for each redox zone (Fig. 3B) further revealed large overlaps in abundant ASVs between the two trenches. Thus, even with our expansion of the analysis we reach a similar conclusion as Peoples and coworkers that endemism must be relatively rare in hadal sediments. However, the overlap between the trenches decreased from the oxic to the nitrogenous and ferruginous zones. While individual redox zones in these two geographically isolated hadal trenches provide similar ecological niches and are to a large extent inhabited by the same abundant ASVs, this decrease of core microbiome overlaps may be driven by enhanced dispersal barriers, as discussed in the previous paragraph.Fig. 3: Microbial community composition across trenches.A Relative read abundances (%) on phylum/class level of the ten most abundant taxonomic groups (universal 16S rRNA gene data) grouped by individual redox zones in hadal samples of the Kermadec and Atacama trenches. Both the color gradient and the number within the squares indicate the average relative read abundances within the respective sample group. B Number of ASVs and relative fractions of total reads constituted by the core microbiomes of the oxic, nitrogenous, and ferruginous zones, respectively, as unique to the Atacama Trench (blue), unique to the Kermadec Trench (yellow), and shared between trenches (purple).Full size imageUnexpectedly, the phylum-level composition and depth distribution at the continental slope (sites A1 and A9) resembled the results from the hadal zone more closely than those from the abyssal plain, with Thaumarchaeota, Alphaproteobacteria, Gammaproteobacteria, and Bacteroidetes decreasing in relative abundance from the oxic to deeper sediment sections, and Chloroflexi increasing with sediment depth. In contrast, at the abyssal sites, the relative abundance of Thaumarchaeota was almost twice as high (A7: 23% K7: 24%) as in the oxic zone of hadal sediments and did not change significantly over sediment depth (Supplementary Fig. 13A). This was particularly pronounced in the archaea-specific dataset, where Thaumarchaeota comprised more than 99% mean read abundance (Supplementary Fig. 13B). However, in contrast to the hadal and continental slope sediments, where increased relative abundance also indicated growth, estimated absolute abundances at the abyssal plain sites generally decreased with sediment depth (Supplementary Fig. 13C). Hence, we propose that the downcore changes in the abyssal plain sediments may reflect differential persistence and survival capabilities rather than growth, similar to conclusions from subsurface sediments [56]. Thus, the conditions for microbial life differ quite fundamentally between abyssal plains and hadal trenches. The similar directional phylum-level changes in the continental slope and hadal sites further supported biogeochemical forcing as a main driver of microbial community composition on the phylum level and suggested that potential effects associated with oceanic depth or hydrostatic pressure are secondary or mainly apply to finer taxonomic levels.When all sites were compared through PCoA of Bray Curtis dissimilarities, both bathyal and abyssal communities differed from hadal samples (Supplementary Fig. 14A), and ANOSIM confirmed this distinction (p  > 0.001, R = 0.595). The archaea-specific dataset showed similar patterns as the universal dataset except with clearer separation between the two trenches (Supplementary Fig. 14B). This analysis indicated a gradient of microbial community composition with increasing oceanic depth, despite the high similarities of phyla compositions between sediments with similar redox stratifications.Focusing on oxic horizons across sites, and thus removing the strong effect of the redox gradient, the abyssal samples again showed high similarities to each other and to the bathyal site, while the communities of the hadal zone of each trench clustered separately (Supplementary Fig. 14C, D). Still, ANOSIM indicated a clear separation of hadal from shallower samples (p  > 0.001, R = 0.677) with less variation within the individual groups. These patterns were also reflected in the overlaps of core microbiomes of all oxic samples, in which adjacent realms shared more ASVs (Hadal–Abyssal: 37 ASVs; 7% of all reads; Abyssal–Bathyal: 26 ASVs; 3.1%) than the hadal sites and bathyal site (6 ASVs; 0.5%), in addition to the 30 core ASVs (9.2%) found in all realms (Fig. 4B and Supplementary Fig. 15). The relatively small overlap of core ASVs between the hadal and bathyal sites indicates a gradient in community composition of the oxic zone across depth realms with respect to the more abundant members. Factors that could impose such a barrier on core microbiome constituents and benthic microbial communities in general are discussed in the next section.Fig. 4: Microbial community composition across benthic realms.A Principal coordinate analysis (PCoA) of Bray Curtis dissimilarity across samples from the oxic zone (CR sectioning) from the hadal (yellow), abyssal (turquoise), and bathyal (purple) realms in the Kermadec Trench (triangles) and Atacama Trench (circles) based upon the universal 16S rRNA gene dataset. B Number of ASVs and relative fractions of total reads constituted by the core microbiomes of the oxic zones of the hadal (yellow), abyssal (purple), and bathyal (turquoise) realms.Full size imageFactors controlling community composition in hadal vs bathyal and abyssal sedimentsPrevious studies on hadal trench sediments suggested that geochemical factors had a stronger impact on community composition than, for instance, hydrostatic pressure [24]. In this section we aim to test previous hypotheses by determining how well TOC concentration and redox zonation explain variation in the microbial communities. We start by excluding potential confounding effects of oceanic depth and geographic isolation by focusing on the Atacama Trench.Dissimilarity within a trenchIn the Atacama Trench, the ordinations of Bray Curtis dissimilarity already hinted that factors associated with sediment depth and redox zonation were the driving forces of microbial community composition (Fig. 2A, B). Previously, it was shown that variation in TOC concentration (ranging from 0.3 to 1.5%) was one of the best predictors of community variation in abyssal and bathyal sediments [6, 57]. In the Atacama Trench, TOC concentration decreased from the northernmost site A10 (1.44 ± 0.35%; downcore average ± SD) to the southernmost A6 (0.44 ± 0.09%; A6) and this decrease coincided with a decrease in metabolic activity along the trench axis [22, 26]. TOC concentrations also fluctuated with increasing sediment depth at each site, most pronouncedly at sites A2 and A10, where values peaked at around 9 cm depth and varied downcore between 0.3–0.9 and 0.7–2.0%, respectively [22].We delineated the effects of redox zonation from site–site variation and TOC concentration on microbial community composition using variation partitioning on Hellinger-transformed ASV counts (Fig. 5A and Supplementary Fig. 16A). The unique fraction of variation statistically explained by TOC was very low (1%, p = 0.014) yet had a large overlap of 4% with the site-to-site variability. This overlap disappeared completely when A10 was excluded, hinting that much of this trend was driven by high TOC concentrations at this single site. Thus, TOC was a poor predictor of microbial community composition in the Atacama Trench, despite the high downcore fluctuations and the broader concentration range along the trench axis than across all locations of the global dataset on abyssal and bathyal surface sediment of Bienhold et al. [6]. Instead, redox zonation explained the largest unique fraction of variation (24%, p  More

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08 June 2021

Indigenous lands: make Brazil stop mining to secure US deal

Glenn Shepard

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Glenn Shepard

Emílio Goeldi Museum, Belém do Para, Brazil.

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Just before the global leaders’ climate summit in April, Brazil’s President Jair Bolsonaro promised the United States that he would reduce deforestation in the Amazon, hoping to secure a billion-dollar aid package. In my view, any such cash-for-conservation deal should be contingent on Bolsonaro withdrawing his February bid to legalize mining on Indigenous lands.Bolsonaro has met with pro-mining Indigenous leaders in a crusade for economic development, despite evidence that mining in Brazil does not bring lasting improvements to socio-economic indicators (see go.nature.com/2s6zknt; in Portuguese). Granting current requests for mining concessions would affect 30% of Brazil’s Indigenous lands.Heavily armed illegal gold miners are invading federally protected Indigenous lands with impunity, knowing that the president has their back. In a shoot-out last month with Yanomami Indigenous people in the state of Roraima, miners fired at community members and Federal Police agents.Given Brazil’s current economic devastation, the administration of US President Joe Biden is in a strong position to seek major concessions to secure the aid deal. High on that list should be stopping illegal incursions and reversing plans to legalize mining on Indigenous lands.

Nature 594, 177 (2021)
doi: https://doi.org/10.1038/d41586-021-01522-w

Competing Interests
The author declares no competing interests.

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We surveyed small mammal communities in a montane area along the elevational gradient in relation to habitat characteristics and human impact, this study being the first to assess habitat use by small mammals in the Southern Carpathians.Compared to a similar study conducted in the Eastern Tatra Mountains31, the species richness (12 species captured) was lower in our survey; part of the reason could be that the North Carpathian endemic Microtus tatricus and the boreal species Sicista betulina are absent in our study area, which is beyond the limits of their geographical distribution. Species composition of small mammals was overall comparable to those reported for forested areas of Northern Carpathians17,32,33, although a high variability, both spatial and temporal, in the number and abundance of species characterized all surveyed communities. Although A. flavicollis was seldom captured in 2003 and 2005 and only at low elevations23, overall it, together with M. glareolus, dominated the small mammal community, representing over 75% of the captured individuals (Table 1). This is the common pattern of small mammal communities in temperate zones, i.e., to be dominated by two species, usually rodents34,35,36. M. glareolus and A. flavicollis are the dominant species in most forests of central and eastern Europe32,33,37,38, with one or the other being more numerous depending on habitat conditions and geographic position35. M. glareolus and A. flavicollis were also found to remain dominant in small-sized clearings39.Box-trapping results for shrews are often considered underestimates because of their small size40 and because seed baits are not attractive to them41. However, during our survey S. araneus had wider distribution than A. flavicollis; we captured it in low numbers in a large number of trapping sites, having the highest ratio between occurrence (45.2%) and relative abundance (16%) of all small mammal species (Table 1). S. araneus was higher in abundance in our research area in comparison to both natural and planted montane forests in Northern Carpathians17,32,33, possibly as an effect of the long-term conservation practices in the national park.Besides the three dominant species and S. minutus, all the other captured species are of regional conservation interest, being included in the Red Book of Vertebrates from Romania42, which highlights the conservational value of this landscape.Small mammals showed significant responses to habitat characteristics at population and community levels, regardless of the metrics considered. Tree cover was an important predictor for small mammal communities (Table 2, Table 3). Increased tree cover limits light available for understory plants, reducing habitat structure43, hence the usually negative correlation between canopy cover and both shrub and herbaceous cover. The reduced vegetation complexity of closed-canopy forests may limit resources important to small mammals. Most studies show that forests with a greater percentage of tree cover harbour less abundant small mammal communities44. In the Sierra Nevada mountains in North America, small mammals showed a limited response to canopy thinning, reflecting the generalist habits of the common species in those forests, which may be a legacy of more than a century of human impacts generating a process of biotic homogenization via differential success of some native species over the others45. In Europe, there is a legacy of much longer human impacts, thus common forest species should have even more generalist habits. However, in our research area tree cover was positively correlated with all parameters, except for the abundance of A. flavicollis, which did not significantly respond to it (Table 2). The small mammal fauna in our study area is a primarily forest fauna, with dominant species responding negatively to the decrease in tree canopy cover, even when this means an increase in the understory cover and complexity. The response to tree cover was strongest in M. glareolus (Fig. 2a, Fig. 3). In boreal forests of Scandinavia tall vegetation and structural heterogeneity of trapping stations positively influenced the total abundance of this species15. This may mean that there is an important geographic variability in the ecological behavior of M. glareolus. There are differences in the habitat preferences not only along the latitudinal gradient15,35,46,47 but also on elevation. At the foothills of Southern Carpathians M. glareolus is limited mainly to forest edges and riparian forests with tall hygrophilous vegetation48. During this study we did not find a significant effect of the interaction between elevation and tree cover, probably because of the relatively short elevational gradient (of 1200 m), which did not include lowland forests outside the ecological optimum of M. glareolus. The short gradient may also explain the lack of response by M. glareolus, both as absolute and relative abundance (Fig. 3) to elevation itself, although this species is known to increase in density towards the north and at higher elevations35.Although shrub cover is an important element of vegetation structure, and one which increases its complexity, it had a significant effect only on the abundance of A. flavicollis. In opposition to our expectations, we found increased abundances of A. flavicollis in forests with little or no shrub layer (Table 2). In forests, shrubs may serve as shelter for mice against physical disturbances such as soil compaction, trampling or rooting49, although some studies failed to find evidence for this50. A positive effect of cover and height of shrub layer was also found on the abundance of A. flavicollis in the Northern Carpathians in forest clearings51. However, besides the positive effects of greater vegetation complexity and increased availability of food and shelter resources, the shrub layer also reduces visibility and hinders rapid movement, so that mobile species such as mice, which rely on running rather than hiding to escape predation, are exposed to higher predation risk in habitats with dense undergrowth.The feature related to habitat heterogeneity to which small mammals responded positively in our study area was the abundance of rocks (Fig. 2a, Table 2). Rocky outcrops and large boulders are stable elements of the landscape that enhance the availability of shelters and refuges providing hard protection for nest sites50. Some species that do not burrow are dependent on rocks for shelter, occurring only in rocky sites. Among these is C. nivalis, but the small number of captured individuals did not allow testing its habitat use.Unlike rocks, woody debris is more ephemeral, and apparently it was less valued as a shelter resource (Table 3). Many studies show the importance of coarse woody debris as a quantitative habitat feature for forest small mammals44; their value increases in the late decay stages52. Woody debris in mid-to-late decay state is often a suitable substrate for lichen and fungi, and can support a rich insect fauna53, all potential foods for omnivorous rodents and shrews. In our research area the sites with the largest amounts of coarse woody debris were those recently logged, so availability of food resources for small mammals was not optimal.Soil moisture, which has a very strong effect on the primary productivity and vegetation diversity, may also have an important role in the habitat selection, with various effects on small mammal populations. In our study area the two dominant rodents had opposite responses to soil moisture, with M. glareolus showing a strong preference for dry habitats (Fig. 3, Table 2), in contrast to its response to moisture in other parts of its distribution. At the southern limit of its geographical distribution35 or at the limit of its elevational distribution48, M. glareolus is usually confined to damp habitats, but there it does not develop abundant populations, with Apodemus species usually dominating the small mammal community. In the northern part of its distribution, where Apodemus species are absent, M. glareolus also shows a preference for moist woodlands54. We may thus infer that the response of M. glareolus to soil moisture is modulated by the interaction with mice species, in our case A. flavicollis. This conjecture is also supported by the fact that moisture did not significantly affect community abundance, only species composition (Table 3). Other studies have also reported conflicting results of the role of soil moisture for A. flavicollis. For example, it was one of the most important factors influencing population dynamics of A. flavicollis in a beech forest in northern Germany55 but it did not predict its distribution in Britain56.Sites closer to watercourses are damper, so an overlap of the effect of the two variables—moisture and distance to water—would be expected. However, the significant negative effect of distance to water on the abundance of A. flavicollis also had a component that was independent of soil moisture (Table 2), and this may have a spatial significance. The increased abundance of A. flavicollis in sites close to watercourses could be explained by a potential fence effect that these may exert on small mammal populations. River banks are linear habitats bordered on one side by a physical barrier, more or less penetrable depending on the local habitat morphology. Linear habitats with favourable conditions sometimes shelter rodent populations at densities much higher than those in wide habitats, although the underlying mechanism, involving probably territoriality and dispersal, is not yet understood57. In our research area, river banks were important for A. flavicollis especially in low abundance years, when we captured this species exclusively here and only at low elevations, suggesting that besides a source of habitat heterogeneity watercourses may be involved also in the spatial dynamics of populations, with their banks being used as routes for dispersal.Neither species richness nor species abundance changed along the elevational gradient in our research area when also considering yearly fluctuations and habitat characteristics (Table 2), and our result is in contradiction with the pattern frequently described for mountains worldwide58,59, including the Eastern Tatras31, which shows a reduced species richness with the increase in elevation. But on the other hand, we found species composition to be affected by elevation, with A. flavicollis responding negatively and S. araneus positively. The thermophilous character of A. flavicollis is more evident in the Northern Carpathians, where this species was found only up to 1328 m, well below the timberline31. But as latitude compensates for elevation, at least in part, in our research area A. flavicollis was found along the entire elevational gradient, up to above 2000 m (Table 1), beyond the timberline, in the subalpine shrubs, perhaps as a result of its lack of preference for the tree cover. S. araneus had a similarly wide elevational distribution and, unlike A. flavicollis, it was captured at high elevations also in low abundance years23. This result supports the classification of S. araneus as a habitat generalist. In contrast to these species, M. glareolus was only once captured in the shrubs beyond the timberline, suggesting that in our study area this vole avoids habitats with no tree layer. This may also be because the subalpine sites that we surveyed were heterogenous, with relatively small patches of shrubs separated by open meadows, areas avoided by M. glareolus.Logging is the main human activity causing disturbance of forests. In our study area only selective logging was recent, while older clearcuts were already reforested. The overall impact was negative and significant on species richness and total abundance, as well as on the abundance of S. araneus. The sensitivity of S. araneus to logging may be one cause of its increased abundance at higher elevations, as in the study area recent timber exploitation was concentrated at low elevations (mostly in mixed forests). Although we did not find a significant response of M. glareolus to logging, other studies revealed that this species is influenced by habitat alterations caused by logging15 but also by the inter- and intraspecific competition, which is considered by some investigators to be the main mechanism causing the decline of vole populations in harvested forests60. We learned that timber exploitation caused a drastic reduction of the small mammal populations in the disturbed area, to the point where no animal was captured during a trapping session, with the neighbouring habitats being also affected. However, since habitat changes were not substantial, timber extraction had a relatively short time impact on the small mammals, and the year following logging the community structure resembled that of undisturbed areas. This suggests that selective logging with the extraction of a relatively small amount of timber affects small mammals rather by direct disturbance than by changes in habitat characteristics. The influence of logging on species of conservation interest, such as the mostly arboreal M. avellanarius and the rare S. alpinus, still needs to be evaluated. The main effect of logging is the decrease in canopy cover or its complete removal in case of clearcuts. But there are also other effects, such as degradation of shrub and herbaceous layers, soil compaction and erosion, and also direct disturbance involving presence of humans and sometimes domestic animals (in the research area logged trees were removed by horses and watch dogs usually roamed the logged forest patches and their surroundings), noise and soil vibrations. Following reduction of canopy cover, improvement in light conditions cause development of understory and decrease of soil moisture, affecting the abundance and composition of animal communities. Most studies on the influence of forest management on small mammals in Europe have focused mainly on clearcutting, one of the most common methods of forest harvest, and have revealed a positive effect on most analyzed small mammals, which can be attributed to an increase in forb and grass cover in the harvested areas61. In managed forest in Czech Republic it was found that the practice of felling within relatively small-sized clearings may help preserve the diversity of small mammal community39. However, the observed positive effect of clearcuts may be a biased result caused by the fact that most surveyed sites were in homogenous conifer plantations, a low-quality habitat for small mammals61.We found that tourism had less impact on small mammals compared to logging, with M. glareolus showing the only significant negative response. Tourism may also represent an additional source of food for the small mammal species that tolerate the presence of humans, such as A. flavicollis, which we found on campgounds. Touristic buildings may also represent important daily or hibernation shelters for some rodents, such as Glis glis, which we observed in autumn in a chalet. In contrast to logging, the effect of tourism on small mammals has been less researched and most such studies have focused on winter sports resorts and mainly on the impact of ski-run development, which involves substantial alteration of forest habitat, sometimes with a significant change in small mammal communities62. In case of ecotourism, damage to the vegetation and soil compaction that result from trampling during tourist season is only local and temporary, thus the regeneration of soil fauna and vegetation is possible63, hence the weaker effect of ecotourism on small mammals.Habitat characteristics had a stronger influence on community abundance than on species composition (Table 3), suggesting that, being primarily forest dwellers, the small mammal species in our study area have somewhat similar responses, especially towards tree cover, but they also show some differentiation, which is reflected by the divergent responses of A. flavicollis, M. glareolus, and S. araneus in their relative abundances in the community. The differences in the relative habitat use, along with the divergent dietary niche, enables their coexistence as dominant species, exploiting the same wide range of habitat resources.In conclusion, habitat use by small mammals in the continuous forest landscape in the Southern Carpathians was overall similar to that reported from the Northern Carpathians, with some notable differences related to recent and historical forest management practices and to latitude. Variation partitioning showed that yearly fluctuations were more important than habitat selection in shaping community composition. Temporal variations eclipsed the effects of habitat selection and elevational gradient, temporal fluctuations in community abundance and species composition having higher amplitudes than spatial variations. Relative habitat use by most species also changed among years. 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