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Acta Botanica Brasilica

Print version ISSN 0102-3306On-line version ISSN 1677-941X

Acta Bot. Bras. vol.33 no.1 Belo Horizonte Jan./Mar. 2019  Epub Nov 29, 2018 


Local environmental controls of Atlantic Forest tree community assembly on a coastal continental island in southeastern Brazil

Felipe Cito Nettesheim1  *

Mário Luís Garbin2

Marcos Gervasio Pereira3

Dorothy Sue Dunn de Araujo4

1 Programa de Pós-Graduação em Ecologia, Laboratório de Ecologia Vegetal, Universidade Federal do Rio de Janeiro, 21941-971, Rio de Janeiro, RJ, Brazil

2 Programa de Pós-Graduação em Ecologia de Ecossistemas, Laboratório de Ecologia Vegetal, Universidade Vila Velha, 29102-920, Vila Velha, ES, Brazil

3 Laboratório de Gênese e Classificação de Solos, Departamento de Solos, Instituto de Agronomia, Universidade Federal Rural do Rio de Janeiro, 23890-000, Seropédica, RJ, Brazil

4 Sistemática Vegetal, Instituto de Pesquisas Jardim Botânico do Rio de Janeiro, 22460-030, Rio de Janeiro, RJ, Brazil


Tropical forests with high species diversity are commonly found in rugged montane areas. We investigated causes of local tropical forest tree community assembly on a continental island with heterogeneous terrain. We recorded tree community (absolute species abundance), topography, soil, litter and location in 40 sampling units on two opposite sides of the island with similar heterogeneous terrain. We used transformation based Redundancy Analyses and variation partitioning to determine the contribution of environment (topography, soil and litter), spatial structure (geographic location and Moran Eigenvector Maps) and the shared effects of these to explain community assembly. The environment made a significant contribution to explain tree community patterns (species composition and abundance) across all models. Conversely, spatial structure showed minor impact. Contribution of strictly environmental effects and spatially structured environmental effects varied when evaluating each site independently as well as when evaluating the combined data. Evidence suggests that local tropical tree community assembly on heterogeneous terrain may be located much closer to the niche end of the hypothetic niche-neutral continuum. Findings indicate additionally that heterogeneity of environmental factors present in dissected mountainous terrain can affect the way tropical community assembly processes are perceived.

Keywords: community composition; community structure; floristics; neutral; niche; soil; spatial structure; topography; tropical forest


Understanding the ecological processes that control species distributions and natural community assembly is a fundamental goal of community ecology deeply rooted in the theoretical foundations of this discipline (Tilman 2004). Niche-assembly and dispersal-assembly theories represent two contrasting perspectives in this regard (Chave 2008). While the former is based on interspecific competition (Tilman 1982) and environmental filtering (Grimme 1977) as the main structuring processes (Chase & Leibold 2003), a prevalent example of the latter (e.g. the Unified Neutral Theory of Biodiversity and Biogeography; Hubbell 2001) proposes that natural communities arise as a consequence mainly of stochastic demography, speciation and dispersal (Etienne & Alonso 2007; Leigh 2007). A long lasting debate over which perspective (niche or neutral) is more suitable to explain community assembly leads to a focus on disentangling the relative contribution of environmental filters (henceforth environmental conditions) and stochastic processes (e.g. dispersal-limitation) that originate spatially structured species distributions (Chave 2008; Clark 2012; Dray et al. 2012; Rosindell et al. 2012). This understanding is represented by hypotheses such as the niche-neutrality continuum, which suggests communities are located somewhere on a hypothetical axis according to the inputs that niche and neutral processes provide to their assembly (Tilman 2004; Gravel et al. 2006; Leibold & Mcpeek 2006). Determining where communities lie within this continuum is a key question in ecology to advance comprehension of the mechanisms behind species distribution and community assembly.

One pattern that has puzzled ecologists for decades is the high number of species in plant communities of tropical forests, in particular those covering the dissected landscape of mountain chains (Morley 2000; Richter 2008). The heterogeneous terrain of such areas displays abrupt land surface changes that affect a variety of environmental conditions (e.g. topography, soil, litter, climate) commonly associated with patterns of richness, distribution, and coexistence of plant species (Chase & Leibold 2003; Richter 2008; Jones et al. 2011; Hofer et al. 2008; Baldeck et al. 2012; Eisenlohr et al. 2013). Still, few studies have focused on disentangling the contribution of niche-related predictors (e.g. environmental conditions) and neutral-related predictors (e.g. spatial structure) to explain tropical tree community assembly at local-scale (< 20 km2) heterogeneous terrain (Svenning et al. 2004; Baldeck et al. 2012; Cielo-Filho & Martins 2015). Most addressed this issue at large-scale (> 100 km2) or by focusing on ferns and lycophytes instead of trees (Jones et al. 2011; 2013; Bergamin et al. 2012; Eisenlohr et al. 2013; Rezende et al. 2015; Saiter et al. 2015; Arellano et al. 2016; Nettesheim et al. 2018). Studies of tropical tree community assembly at smaller local-scale are necessary to build comprehensive knowledge of niche- and neutral-related effects across different scales.

Brazilian Atlantic Forest remnants can yield important insights for this discussion because they are commonly located on mountain chains with highly heterogeneous terrain (SOS Mata Atlântica 2015). Studies showing the contribution of environmental conditions and spatial structure to explain plant community assembly in this forest have begun to appear recently (Bergamin et al. 2012; Eisenlohr et al. 2013; Cielo-Filho & Martins 2015; Oliveira-Filho et al. 2015; Rezende et al. 2015; Saiter et al. 2015; Nettesheim et al. 2018). Most of these studies indicate a greater role of niche-related environmental effects when compared to neutral-related spatial structure effects to explain vegetation changes. However, an opposite trend was found in the only study carried out within a local-scale in this forest (Cielo-Filho & Martins 2015); this study did not sample soil data (instead using topography as a surrogate) on a scale where soil particularly is expected to be relevant to community assembly (John et al. 2007; Baldeck et al. 2012; Chang et al. 2013). There is mounting evidence indicating that Atlantic Forest tree community assembly benefits from environmental conditions associated with abrupt terrain changes across the heterogeneous mountainous landscape where it occurs. This suggests that even small terrain variation such as a slight surface change in slope orientation is sufficient to determine different environmental conditions (e.g. distinct amounts of sunlight incidence; see Nettesheim et al. 2015) which increase the array of habitats for the tree community. Understanding how heterogeneous terrain is related to the behavior of local-scale community assembly may provide valuable insight into the mechanisms behind the high number of species and high levels of endemism reported for the Atlantic Forest.

Diverse Atlantic Forest along the coast of southeastern Brazil is commonly found on dissected heterogeneous mountain ranges. In fact, a mountain range in this region has been named a plant diversity hotspot of particular interest within the Atlantic Forest (Murray-Smith et al. 2009). Perhaps such high levels of plant diversity and endemism are due to a wide array of environmental conditions provided by the rough terrain of the mountain range. In this study, we address the causes of tree community assembly at the local-scale by evaluating a tropical continental island that displays the typically heterogeneous terrain of a mountain range covered by Atlantic Forest in southeastern Brazil. We determined if the role of niche-related environmental conditions (topography, soil and litter predictors) and neutral-related stochastic processes (spatial structure predictors) to explain tree community patterns (species composition and abundance) is comparable between sites with similar heterogeneous terrain but facing opposite geographic orientation. We also wanted to determine if assessing the combined data from both sites (greater local-scale evaluation) would yield comparable roles to the ones detected for each site independently (smaller local-scale evaluation). We hypothesized that the role of niche-related processes are altogether more important than the role of neutral-related processes for local tropical tree community assembly in areas with heterogeneous terrain; however, the scale of observation can affect our perception of these roles. Therefore, we expected that environmental conditions would be more important than the spatial structure regardless of the evaluated data (each site or combining the sites) and that the contribution of niche- and neutral-related processes would be similar for each site independently but not when sites are combined.

Materials and methods

Study area

We conducted investigations on the continental island of Marambaia (henceforth, Marambaia) in Rio de Janeiro State, Brazil (Fig. 1, 23º4’26”S 43º58’25”W). This island is covered by Atlantic Forest and located within the Serra do Mar mountain range region known for its high levels of plant diversity and endemism (Murray-Smith et al. 2009). The Atlantic Forest covers about 22 km2 of this continental island and is classified as dense sub-montane ombrophilous forest (IBGE 2012). Mean annual precipitation is 1240 mm and the average temperature over the year varies from 20.9 ºC to 26.9 ºC (Menezes et al. 2005). The origin of Marambaia is associated with geological evolution of the Serra do Mar mountain range; soils here cover the same crystalline gneiss parent material that underlies the Atlantic Forest across this mountain range (Almeida & Carneiro 1998; Menezes et al. 2005). Although Marambaia ranges over less altitude (0 to 641 m) than continental sections of Serra do Mar, it is marked by the typical heterogeneous terrain displayed by this mountain range (Nettesheim et al. 2015). The heterogeneous topography of Marambaia is characterized by a main ridge stretching across its mountainous terrain (Fig. 1).

Figure 1  The study area (continental island of Marambaia - 23⁰4’26”S 43⁰58’25”W) is located in Brazil. Detailed maps show the location of the island in the state of Rio de Janeiro. The refined terrain image shows the heterogeneous terrain at the island and sites A and B (separated by a white line). The lower images show the location of the plots at sites A and B. 

Data collection

We recorded tree community data from January 2004 to December 2005 at two distinct sites (faces) of the mountainous Marambaia terrain (Fig. 1). These two sites have similar environmental conditions; Site A does not face the open sea and is mainly oriented in a northwest direction (henceforth, dataset A), while site B faces the open sea and is mainly oriented in a southeast direction (henceforth, dataset B). We further combined dataset A and dataset B into a single dataset (henceforth, dataset A-B) which therefore represents greater local-scale evaluation than either dataset alone and encompassed a wider range of environmental conditions.

We used 50 m × 2 m sample plots. We established 20 (100 m2) plots at site A (0.2 ha) and 20 plots at site B (0.2 ha), for a total of 40 plots (4000 m2 or 0.4 ha) representing the island (Fig. 1). The plots were established during randomized walks based on accessibility and representation of vegetation and topographic variation on each side of the main ridge. After reaching a location for a given plot we tossed a six-sided die to determine the direction of establishment of the longest side of the plot (in a circle - number obtained in dice multiplied by 60 degrees). We used a GPSMAP Garmin® 76CSx (Garmin International Inc., Kansas City, USA) to keep plot centers at least 50 m apart from each other. Inside the plots we recorded data on the identity and number of all tree species with trunk diameter of at least 5 cm at breast height (diameter at breast height - dbh ≥ 5 cm), along with topography, soil, litter and spatial structure (geographic location) predictors.

We recorded elevation above sea level (Elev), terrain slope angle (Slp) and annual amount of direct solar radiation (SoR) as topography (environmental) predictors. We used GPS to obtain Elev and a Geographic Information System (GIS) technique relying on a 1 arc second (~30 m resolution) raster image (South American Datum 1969 / UTM - 23S - coordinates) of the area (Valeriano & Rossetti 2011) to obtain Slp and SoR values for each plot (based on geographic location). We sampled and determined a total of 18 soil and litter (environmental) predictors (Tab. 1) within each plot (see detailed description of methodology in Nettesheim et al. 2015).

Table 1  Soil and litter predictors measured in each plot. The table shows the method used to quantify each soil and litter predictors. Acronyms used to identify each of the recorded predictors in the analyses are also shown (for linear and quadratic forms). 

Soil and litter factors Method of quantification / extraction Linear factors acronyms Quadratic factors acronyms
pH 1 : 2.5 soil : H2O suspension pHsoil pHsoil 2
Organic Carbon walkley and black method Csoil Csoil 2
Nitrogen semi-micro kjedahl method Nsoil Nsoil 2
Phophorus solution: H2SO4 0.0125 mol L-1 + HCl 0.05ml L-1 Psoil Psoil 2
Potassium solution: H2SO4 0.0125 mol L-1 + HCl 0.05ml L-1 Ksoil Ksoil 2
Sodium solution: H2SO4 0.0125 mol L-1 + HCl 0.05ml L-1 Nasoil Nasoil 2
Extractable acidity solution: 0.5 mol L-1 calcium acetate at pH of 7 H+Alsoil H+Alsoil 2
Calcium (Ca2+) solution: 1 mol L-1 KCl Casoil Casoil 2
Magnesium (Mg2+) solution: 1 mol L-1 KCl Mgsoil Mgsoil 2
Aluminum (Al3+) solution: 1 mol L-1 KCl Alsoil Alsoil 2
Sand (%) pipette method sandsoil sandsoil 2
Clay (%) pipette method claysoil claysoil 2
Silt (%) pipette method siltsoil siltsoil 2
Nitrogen in litter sulfuric digestion, semi-micro kjeldahl method Nlitter Nlitter 2
Potassium in litter sulfuric digestion, flame photometry Klitter Klitter 2
Calcium in litter sulfuric digestion, atomic absorption spectrometry Calitter Calitter 2
Phosphorus in litter sulfuric digestion, colorimetric method Plitter Plitter 2
Magnesium in litter sulfuric digestion, atomic absorption spectrometry Mglitter Mglitter 2

We first approached the spatial structure of the data based on each plot center coordinate (Longitude - X and Latitude - Y; Legendre & Legendre 2012). However, this is a rougher type of spatial structure mostly appropriate to detect linear spatial trends (henceforth linear spatial structure). It does not allow modeling more refined patterns that can arise due to stochastic effects (e.g. patchy spatial structures). Thus, we centered the linear spatial structure (X and Y) and synthesized a set of refined (distance-based Moran Eigenvector Map; henceforth, dbMEM) spatial structure predictors (Legendre & Legendre 2012). We synthesized dbMEMs independently for dataset A, dataset B and dataset A-B and only kept dbMEMs with positive Moran´s I (Moran´s I greater than expected Moran´s I).

Data analysis

We began analysis by calculating the quadratic form of each recorded environmental predictor to allow modeling unimodal associations. We did this because all the recorded raw topography, soil and litter predictors are appropriate to model linear associations with the response data, but they are poor in deducing unimodal trends (Jones et al. 2008). We used orthogonal second order polynomials to expand all raw linear environmental predictors into their quadratic forms. Final set of quadratic soil and litter predictors can be seen in Table 1; these also include Elev2, Slp2, SoR2 (not shown in Tab. 1).

We then organized the tree community, topography, soil and litter data into the following data matrices (independently for dataset A, dataset B and dataset A-B): community response matrix (species abundance - absolute number of marked individuals - in each plot); environmental (E) explanatory matrix (raw - linear - and quadratic topography, soil and litter predictors in each plot); linear spatial structure (SL) explanatory matrix (X and Y geographic coordinates of each plot); and refined spatial structure (SR) explanatory matrix (positive dbMEM predictors for each plot). We excluded all species that occurred in less than five plots from the community response matrices; all subsequent analyses rely on parametric regressions that should, ideally, be estimated with at least five data points for each response variable - species. A lower cut threshold could lead to biased results due to a greater chance of skewed data points. Additionally, the adopted cut ensures greater focus on the main dominant species and trends of the community and their association with the environment (see Wagner 2003 and Garbin et al. 2012 for similar procedures in this regard). We used the Hellinger transformation for all community response matrices (Legendre & Legendre 2012).

Before running independent transformation based Redundancy Analysis (tbRDA) and variation partitioning for datasets A, B and A-B, we performed a variable selection of environmental and spatial structure (linear and refined) predictors independently for each dataset. The selection of environmental factors initially consisted of detecting high collinearity (r > 0.7) among all chosen environmental factors (multicollinearity should be avoided before performing automated variable selection procedures; Legendre & Legendre 2012; Dormann et al. 2013). We discarded highly correlated predictors (one at a time) based on relevance to explain tree variation in the study area; and continued dropping environmental predictors until there were no more correlations (r) > 0.7 and the Variation Inflation Factor of remaining predictors was smaller than 5. We finished the selection routine of environmental predictors by running a forward selection procedure using the remaining set of predictors and relying on the two stopping rules suggested by Blanchet et al. (2008). Variable selection of linear and refined spatial structure factors for datasets A, B and A-B relied only on forward selection because spatial factors are orthogonal to each other.

Finally, we ran complete and partial tbRDAs (Legendre & Legendre 2012) which allowed us to perform variation partitioning to quantify the effects of pure, combined, and shared contributions of environment (E), linear (SL) and refined (SR) spatial structures to explain tree community patterns for each dataset (see Økland 2003 and Legendre & Legendre 2012 for detailed descriptions of variation partitioning for multivariate data). Reported fractions of explained variance represent adjusted fractions of variation (Peres-Neto et al. 2006). We tested the significance of the models with randomization procedures based on 9999 iterations (Legendre & Legendre 2012); we interpreted contribution of model fractions if the complete model was significant. We carried out all analyses in the R 3.2.1 environment (R Foundation for Statistical Computing, Vienna, AT) with functions from the packages vegan, packfor and spacemakeR.


The final factors in the tbRDA to explain tree community patterns for dataset A were Nsoil, H+Alsoil, Mglitter, Ca2 soil, pH2soil, Slp2, Y and dbMEM1_A; for dataset B were Nsoil, Alsoil, C2 soil, Mg2 soil, X and dbMEM1_B; and for dataset A-B were H+Alsoil, SoR, Csoil, Elev, Nlitter, Ca2 soil, Y, X, dbMEM2 and dbMEM1_AB (see Tab. 1 for acronyms). All three models yielded statistically significant relationships and achieved adjusted coefficients of variation between 0.189 and 0.309 (Tab. 2).

Table 2  Results of the variation partitioning routine relying on transformation based Redundancy Analyses to explain tree community patterns. Fractions are shown for each examined dataset (dataset A, dataset B, and dataset A-B). TVE: total variation explained; E: contribution of environmental predictors; SL: contribution of linear spatial structure predictors; SR: contribution of refined spatial structure predictors; ∩: shared contribution; UV: unexplained variation; R2 a: corrected proportions of explained variation; %TVE: percentage of contribution from fractions relative to the total variation explained by the model. Negative fractions are interpreted as zeroes. Significance was determined for each of the three complete models by obtaining the probability that an equal or better model would be encountered at random: P ≤ 0.05*, P ≤ 0.01**, P ≤ 0.001***

Fraction dataset A dataset B dataset A-B
R2 a % TVE R2 a % TVE R2 a % TVE
TVE 0.189** 100 0.309** 100 0.218** 100
pure E 0.113 59.8 0.227 73.5 0.059 27.1
pure SL - 0.016 - 8.5 0.012 3.9 - 0.006 - 2.7
pure SR 0.002 1.1 0.002 0.6 - 0.003 - 1.4
SL ∩ E 0.029 15.3 - 0.028 -9.1 0.056 25.7
SL ∩ SR 0.037 19.6 0.005 1.6 0.028 12.8
E ∩ SR 0.015 7.9 - 0.024 -7.8 0.018 8.3
E ∩ SL ∩ SR 0.009 4.8 0.115 37.2 0.066 30.3
UV 0.857 - 0.691 - 0.782 -

Pure environment was responsible for the greater proportion of explained variation relative to pure linear and pure refined spatial structures in all three models. We did not detect contributions from pure linear and pure refined spatial structures for datasets A and A-B, but they were present (albeit low) for dataset B. The contribution of spatially structured environmental fractions (shared contribution between environment and spatial structure) was present in all three models. The pure environmental fraction was more important than the spatially structured environmental fractions in datasets A and B, but not in dataset A-B. The contribution of shared effects between linear and refined spatial structures (SL ∩ SR) was much higher than from the pure spatial structure fractions in datasets A and A-B; in dataset B it was quite small. These results are detailed in Table 2.

A comparison of overall patterns based on the percentage of variation explained by fractions relative to the total variation explained in each model (Tab. 2) allowed detecting consistent trends in the contribution of niche-related environmental effects and neutral-related spatial structure effects for the three datasets (Tab. 3). The contribution of pure environmental fraction in dataset A-B was, at most, half that was found in dataset A or dataset B (first entry of Tab. 3). Conversely, when all spatially structured environmental fractions are considered together, the contribution of environment-related effects was at least two times greater in dataset A-B than in datasets A or B (second entry of Tab. 3). Following this line of reasoning, if we combine spatially structured environmental fractions with the pure environmental fraction (assuming both represent niche-related effects), niche-related effects remain rather constant among all three models (third entry of Tab. 3). Contribution of neutral-related spatial structure effects also remained constant among the datasets when considering only the pure spatial structure fractions or all the spatial structures together (respectively fourth and sixth entries of Tab. 3). Finally, all ratios between the contribution of niche-related environmental effects and neutral-related spatial structure effects showed that the former are more important than the latter regardless of how the fractions are combined (last three entries of Tab. 3).

Table 3  Contribution of different sources of variation to explain tree community patterns for dataset A, dataset B and dataset A-B. Sources of variation are based on pooling together contribution of fractions determined with the variation partitioning routine (Tab. 2). Values represent the percentage of variation explained relative to the total variation explained by the complete model (Tab. 2) of each dataset. Negative values are interpreted as zeros. 

Source of variation Fractions pooled together dataset A dataset B dataset A-B
Pure Environment “pure E” 59.8 73.5 27.1
Spatially Structured Environment “E ∩ SL” + “E ∩ SR” + “E ∩ SL ∩ SR 28 20.3 64.3
All environmental fractions “pure E” + “E ∩ SL” + “E ∩ SR” + “E ∩ SL ∩ SR 87.8 93.8 91.4
Pure Spatial Structures (Linear and Refined) “pure SL” + “pure SR -7.4 4.5 - 4.1
Shared spatial fractions (Linear and Refined) “SR ∩ SL 19.6 1.6 12.8
All Spatial Structures “pure SL”+ “pure SR” + “SR ∩ SL 12.2 6.1 8.7
Ratio Pure Environment : Pure Spatial Structures (Linear and Refined) “pure E” : “pure SL” + “pure SR 59.8:0 16.3:1 27.1:0
Ratio Pure Environment : Spatial Structure (pure and shared fractions) “pure E” : “pure SL” + “pure SR” + “SR ∩ SL 4.9:1 12:1 3.1:1
Ratio Environment (pure and shared fractions) : Spatial Structure (pure and shared fractions) “E” + “E ∩ SL” + “E ∩ SR” + “E ∩ SL ∩ SR” : “SL” + “SR” + “SR ∩ SL 7.2:1 15.4:1 10.5:1


In this study we corroborate that niche-related environmental conditions (topography, soil and litter) play an overall greater role than neutral-related spatial structure to explain local-scale tropical tree community patterns at two sites with opposite geographic orientation. We also show evidence that the contribution from pure environmental and spatially structured environmental fractions to explain that these tree community patterns can change according to the range of environmental heterogeneity encompassed in the scale of an established sampling design. It should be noted that although our models captured a relatively small amount of response data variation (large residuals), this is normal when modelling tropical vegetation data and does not weaken or diminish the importance of the detected relationships (Braak 1988; Oliveira-Filho & Fontes 2000; Jones et al. 2011; Bergamin et al. 2012; Legendre & Legendre 2012; Rezende et al. 2015; Saiter et al. 2015; Arellano et al. 2016). Additionally, while some studies interpret the residuals (unexplained variation) of their variation partitioning models as a result of stochastic processes (see Liu et al. 2013; Punchi-Manage et al. 2014), we chose to focus solely on that part of the variation explained by the models. Thus, we treated the residuals of our models simply as random variation, sampling error, etc., and avoided providing them with an ecological interpretation (Legendre & Legendre 2012).

Our findings of a greater role for niche- relative to neutral-related predictors are similar to those of other studies carried out at several other Atlantic and Amazonian forest sites (Svenning et al. 2004; Jones et al. 2011; Bergamin et al. 2012; Eisenlohr et al. 2013; Pansonato et al. 2013; Oliveira-Filho et al. 2015; Rezende et al. 2015; Saiter et al. 2015; Nettesheim et al. 2018). These studies confirm the notion that changes in environmental conditions determine habitat filters, which lead important roles in allowing a high number of species to (apparently) thrive in tropical forests (Jones et al. 2011; Baldeck et al. 2012; Arellano et al. 2016). In agreement, our results showed that areas with heterogeneous terrain seem to maximize the influence of environmental conditions (filters) on tropical tree communities. Such areas may exhibit higher levels of heterogeneous environmental conditions that can be decisive in providing habitats relevant to tree species establishment and development. Detection of quadratic environmental effects in all three studied datasets further suggest that heterogeneous terrain exhibits conditions where species response can be better modelled when non-linear relationships are taken into account. This also indicates that at least part of tropical tree community assembly in areas with rough terrain is affected by optimal resource availability. Therefore, it seems reasonable to expect a greater role of niche-related processes (environmental filtering) over topical community assembly as the terrain of areas become increasingly heterogeneous (e.g. higher elevations; see Nettesheim et al. 2018).

Contribution of fractions varied between the datasets to explain tree community patterns. Studies in the Amazon region showed that the extent of environmental gradients can play a central role in determining which factors are important in explaining tree community assembly (Costa et al. 2009; Pansonato et al. 2013). However, our evaluation revealed an interesting trend in the pattern of fraction contributions that can further elucidate our understanding of how environmental gradients affect community assembly. When we pooled together fractions that represent pure environment and spatially structured environment the contribution of environmental-related fractions was high and similar in all three datasets (Tab. 3). However, when these fractions are considered apart (Tab. 3) one may observe an exchange in the overall pattern of contribution between pure environment and spatially structured environment when comparing either dataset A or dataset B with dataset A-B. There is an obvious decrease in the contribution of pure environment with a simultaneous increase in the contribution of spatially structured environment between datasets A or B and dataset A-B. This is likely because dataset A-B encompasses all the heterogeneous environmental conditions existing within the rough terrain of the study area, while dataset A (as well as dataset B) represents only part of this terrain and its heterogeneous environmental conditions. Consequently, the greater influence of spatially structured environmental conditions that ultimately affect tree community patterns could only be detected when evaluating the whole terrain of the study area (dataset A-B). Thus, researchers should be aware that the amount of environmental heterogeneity captured when establishing a sampling design in a given study area (especially on rough heterogeneous terrain) can affect the way processes behind community assembly are perceived.

Our findings also shed light on how to interpret the spatially structured environmental fractions of models from areas with heterogeneous terrain. Shared fractions of explained variation between environment and spatial structure are problematic in variation partitioning because they can either represent niche-related effects mediated by environmental conditions that are spatially structured or neutral-related stochastic effects confounded with environmental gradients (Legendre & Legendre 2012; Arellano et al. 2016). However, the fact that only the pure environmental and spatially structured environmental fractions varied interchangeably while the pure and shared spatially structured fractions remained low and constant strikes as evidence that the spatially structured environmental fraction for the study area can be interpreted as niche-related effects. This is not to say that all shared fractions of explanation between environment and space in variation partitioning models should be inferred as niche-related effects. However, given the conspicuous terrain changes within small distances typically associated with mountainous areas it seems fairly reasonable that studies in tropical areas with heterogeneous terrain assume the relevance of spatially structured environmental fractions as effects of niche-based processes over community assembly.

The absence or weak signal from pure spatial structure fractions within all three models suggest that neutral-related processes such as dispersal seem to play a negligible role over tree community patterns at the study area. However, studies in tropical forests commonly show that pure spatial structure fractions can be important to explain plant community assembly (Svenning et al. 2004; Eisenlohr et al. 2013; Punchi-Manage et al. 2014). The unusual reduced contribution of pure spatial structure effects detected here is explained by the fact that signs of neutral-related effects were mostly represented in the shared fraction between linear and refined spatial structures. Although these spatial structure effects may arguably represent environmental conditions not considered in the models (Gilbert & Bennet 2010; Diniz-Filho et al. 2012; Legendre & Legendre 2012), their small contributions and the extensive set of (linear and quadratic) environmental predictors used here, provides reasonable assurance to interpret them as a signal of neutral-related processes. This shared fraction between linear and refined spatial structure indicates that (at least) some tree species in the area seem to form linearly distributed patches independent from the environment, likely due to stochastic effects (e.g. dispersal limitation). Moreover, the detection of small neutral-related effects may also be a consequence of sampling design. Other studies that relied on plots randomly distributed within their study area also detected smaller contributions from pure spatial structure fractions and higher participation from environmental fractions (Bergamin et al. 2012; Eisenlohr et al. 2013; Arellano et al. 2016). On the other hand, studies that used systematic sampling design (e.g. regular grid) found results in the opposite direction; e.g. higher proportions of spatial structure fractions (Jones et al. 2011; Baldeck et al. 2012; Punchi-Manage et al. 2014). This indicates a potential bias in the results of variation partitioning that can be attributed to the sampling design. Although the (small; particularly the shared) spatial structure fractions support that neutral-related effects hold (at least) a discrete role in local community assembly across heterogeneous terrain, this issue requires further evaluation using regular sampling designs.

The increased relevance of environmental conditions regardless of the evaluated dataset corroborates that topography, soil and litter represent important resources for the plant community in areas with heterogeneous terrain. This is in general agreement with the reported relevance of topography and soil predictors in explaining plant community assembly and in distribution models of tree species in tropical forests (Tuomisto et al. 2003; John et al. 2007; Baldeck et al. 2012; Eisenlohr et al. 2013). On the other hand, this result calls attention to the role that litter chemistry can play in community assembly; representing information which is seldom used in community ecology but proved important for two out of the three current final models. Perhaps, litter predictors are left aside because most nutrients found in this ecosystem component are expected to be lost before being used by plants (Huggett 2007). Nevertheless, findings here suggest that the litter may hold relevant environmental information, which is not usually considered, and can be confounded with the pure spatial fractions. The extent to which litter has similar or greater relevance than soil and topography as explanatory variable for community assembly remains to be determined. These findings support that tropical forests on dissected mountainous landscapes can encompass a broad range of small local-scale niches associated with a heterogeneous terrain that affects independent soil and litter habitat compartments (Baldeck et al. 2012).

Altogether, our evidence corroborates that tropical tree communities distributed across areas with heterogeneous terrain can be expected to lay much closer to the niche end of the niche-neutral continuum. The assessed tree community responded more strongly to the variation of environmental conditions associated with the terrain than to spatial structures associated to stochastic processes. Even though the overall contribution of environmental conditions did not differ between the examined datasets as expected, the independent fractions of pure and spatially structured environment did, suggesting that the amount of environmental heterogeneity embedded in the terrain of a study area (and scale of evaluation) can affect the way we perceive processes governing community assembly. These findings highlight the fact that tropical forests thriving on heterogeneous mountainous terrain are unique research models which can increase our understanding of community assembly processes and species distributions. In this regard, future studies may yield interesting results by addressing how environmental and spatial structure predictors behave to explain plant community assembly across gradients of increasing terrain and environmental heterogeneity.


We thank the Centro de Avaliação da Ilha da Marambaia (Brazilian Navy) for granting access to the area. We thank the colleagues who helped in the field and Pedro C. Silberman for his diligent proofreading of this manuscript. FC received support from CAPES (Brazilian research agency). MLG received support from CAPES, CNPq (Brazilian research agency) and FAPES (Espírito Santo State research agency). Finally, we thank the Associate Editor and reviewers for the valuable insights that improved this manuscript.


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Received: January 24, 2018; Accepted: October 30, 2018

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