Editor: Michael Rex
Species richness, species turnover and functional diversity in nematodes of the deep Mediterranean Sea: searching for drivers at different spatial scales
Article first published online: 7 JUL 2013
© 2013 John Wiley & Sons Ltd
Global Ecology and Biogeography
Volume 23, Issue 1, pages 24–39, January 2014
How to Cite
Gambi, C., Pusceddu, A., Benedetti-Cecchi, L. and Danovaro, R. (2014), Species richness, species turnover and functional diversity in nematodes of the deep Mediterranean Sea: searching for drivers at different spatial scales. Global Ecology and Biogeography, 23: 24–39. doi: 10.1111/geb.12094
- Issue published online: 3 DEC 2013
- Article first published online: 7 JUL 2013
- Europe Commission
- OBAMA project
- The Italian Research for the Sea, Flagship Project RITMARE
- Beta diversity;
- deep sea;
- functional diversity;
- Mediterranean Sea;
- spatial scales;
- species richness
- Top of page
- Materials and Methods
- Supporting Information
Understanding how biodiversity varies at different spatial scales and the drivers behind these patterns is a crucial issue in ecology. This is evident for the deep sea, the largest biome of the biosphere, where there is little information available on the spatial and temporal variability of biodiversity. Here, we investigated the variability and potential drivers of species richness, turnover and functional biodiversity of deep-sea nematodes at a depth of 3000 m across different spatial scales and in two periods of contrasting pelagic productivity.
The Mediterranean Sea.
We used for the first time a hierarchical sampling strategy that includes different spatial scales, from tens of metres (small scale) to hundreds of kilometres (macroscale).
We show that the variability in biodiversity is greatest at the macroscale, although the rate of variability is about two- to three-fold lower than observed for nematode abundance. Also, turnover diversity is highest at the macroscale (and uncoupled from species richness), and significantly decreases to the meso- and local scales. Functional diversity is positively related to species richness and its variability is associated with the change in richness of predators. The drivers of spatial variability of biodiversity are different at different spatial scales. Our data identify the pivotal role of food quantity in the control of variability in biodiversity attributes at the macroscale, while the quality and bioavailability of food sources have a key role in driving beta diversity and biodiversity attributes at small spatial scales. Also, the largest variations in biodiversity attributes at both macroscales and mesoscales are related to periods of high food input from the euphotic zone.
We conclude that changes in food availability, which can also be expected as a consequence of climate change, have a significant impact in setting biodiversity attributes at different spatial scales in the deep sea.
- Top of page
- Materials and Methods
- Supporting Information
Deep-sea ecosystems cover approximately 65% of the world's surface and have a pivotal role in global biogeochemical cycles; however, they are certainly the least explored of the environments on Earth (Costello et al., 2010). Deep-sea benthic biodiversity is closely linked to ecosystem functioning (Danovaro et al., 2008a), such that its conservation is crucial for sustainability of the ecosystem services provided. Understanding the processes that control deep-sea biodiversity patterns at different spatial scales is a central issue in ecology, and determining the ecological impact due to climate change is a priority (Smith et al., 2009; Tittensor et al., 2010, 2011). Since the pioneering work of Jumars (1976), several studies have been carried out on this topic, and the discovery of longitudinal, latitudinal and bathymetric gradients of species richness in the deep sea has revealed conflicting results when different benthic components (e.g. prokaryotes, meio-, macro- and megafauna) and oceanic regions are considered (Rex & Etter, 2010, and references therein). Deep-sea species diversity and composition have been shown to vary globally, regionally and locally, which suggests that changes in environmental factors will influence the community structure at all spatial scales (Stuart et al., 2003; Rex & Etter, 2010). Several studies have investigated the processes that support high levels of biodiversity under natural conditions (Gaston, 2000) and the drivers that lead to changes in species diversity over time or along ecological gradients (Cottingham et al., 2001; Levin et al., 2001; Rex & Etter, 2010). From these studies, it also appears that the same process/driver can have different effects on biodiversity at different spatial scales. For instance, at the local scale, species and energy relationships are generally described according to a hump-shaped curve, in which the number of species increases up to some energy value, above which a further increase of energy promotes decreased diversity; at the regional scale, this relationship might become positive linear (Chase & Leibold, 2002). This not only reinforces the view that there is not a unique spatial scale at which ecological phenomena occur, but also emphasizes the inherent difficulty in linking patterns and processes across different spatial scales (Levin et al., 2001).
For a long time, the deep sea has been considered to be extremely stable in terms of physical and chemical conditions. However, recent evidence has suggested that this ecosystem is much more temporally and spatially variable than previously thought, with potentially important implications for biodiversity patterns (Lampitt et al., 2010; Pusceddu et al., 2010, 2013; Rex & Etter, 2010). Several mechanisms have been invoked to explain the spatial patterns of biodiversity: (1) sediment grain size and substrate/ habitat heterogeneity (Etter & Grassle, 1992; Danovaro et al., 2009, 2010; Bongiorni et al., 2010; McClain & Barry, 2010; Vanreusel et al., 2010; Zeppilli et al., 2012); (2) productivity (Smith et al., 2008; Lampitt et al., 2010; Tittensor et al., 2011; McClain et al., 2012); (3) food resources (Danovaro et al., 2008b; Gambi et al., 2010); (4) oxygen availability (Diaz & Rosemberg, 1995); (5) water currents (Lambshead et al., 2001); and (6) occasional catastrophic disturbances (Levin et al., 2001; Pusceddu et al., 2010, 2013). Nonetheless, all of these factors are subjected to strong scientific debate because they are often site-specific and constrained by local (or regional) conditions (Levin et al., 2001). The recent literature reveals the pivotal role of productivity (in the form of particulate organic carbon input) in shaping deep-sea biodiversity (both as species richness and turnover) along spatial patterns that are related especially to bathymetric gradients (Wei et al., 2010; Tittensor et al., 2011; McClain et al., 2012; Brault et al., 2013a,b). However, the role of the nutritional quality and the diversification of food sources available in deep-sea sediments in influencing the spatial patterns of the different attributes of biodiversity have been little investigated to date (Danovaro et al., 2008b).
Marine ecosystems generally cover very large spatial scales, although they can also have high heterogeneity at small spatial scales (Fraschetti et al., 2008; McClain & Barry, 2010; Vanreusel et al., 2010). Unfortunately, the limited knowledge about the scale of variability in the attributes of the different benthic components in the deep sea does not allow the definition of a general relationship that can describe the spatial patterns of benthic biodiversity and their regulating factors, nor does it allow us to understand whether different attributes of biodiversity show similar patterns at the same spatial scale(s). To fill in these gaps of knowledge, hierarchical sampling designs and multivariate analyses of variance have been used extensively to quantify spatial and temporal variation in species assemblages, and particularly in marine environments (Fraschetti et al., 2005). A variety of regression-based methods have extended this approach to enable the specification of covariates (as potential drivers of biodiversity) and to allow for spatial (or temporal) autocorrelation of the residuals (Beale et al., 2010). The ability to model spatial autocorrelation has provided additional opportunities to distinguish between extrinsic (unmeasured environmental variables) and intrinsic (aggregation and dispersal) causes of variation in diversity distribution (Legendre, 1993; Lichstein et al., 2002). Lichstein et al. (2002) used an interesting approach to unravel spatial dependency between predictor and ecological response variables, which was based on the outcomes of models that accounted for spatial variation at different scales. The procedure required the evaluation of how the apparent importance of environmental predictors changed from models that ignored both large-scale and fine-scale spatial variation (ordinary least squares, OLS) to models that account for large-scale spatial trends (trend surface analysis) and finally to models that also account for fine-scale autocorrelation (conditional autoregressive models). Using this approach, Lichstein et al. (2002) successfully distinguished between local-scale and landscape-scale habitat variables that can account for the breeding–habitat relationships of migrant songbirds.
Here, we investigated the patterns of distribution of deep-sea nematode biodiversity from the macroscale (thousands of kilometres) to the small scale (tens of metres). We used the biodiversity of deep-sea nematodes as a model, as they account for three-fifths of metazoans on Earth and 80–90% of the total abundance in the deep sea. Moreover, although comparative studies are rare, deep-sea nematode diversity appears to be related to that of other benthic components, including Foraminifera (Gooday et al., 1998), macrofauna (Levin et al., 2001) and the richness of higher meiofaunal taxa (Danovaro et al., 2008a). Nematodes are also characterized by a very high species number (more than a million species; Lambshead, 2004) and the morphological features of their buccal apparatus allow the identification of their feeding habits, which thus provides an important insight into their functional diversity (Soetaert & Heip, 1995; Danovaro et al., 2008a).
Our sampling design was defined to address the following questions: (1) What is the spatial scale at which most of the variability in nematode species richness, turnover and functional diversity occurs? and (2) What are the factors that drive the different attributes of nematode biodiversity at the different spatial scales?
Materials and Methods
- Top of page
- Materials and Methods
- Supporting Information
The Mediterranean Sea
The Mediterranean Basin is c. 3680 km long, with an average width of only 700 km. It is conventionally divided into the western and eastern basins, which are geographically separated by the strait of Sicily. These two basins are also characterized by different benthic topographies, with the western Mediterranean consisting of two distinct deep basins (namely the Algero-Provençal and the Tyrrhenian Sea basins) and the eastern Mediterranean including several distinct deep basins that are located below the Ionian, South Adriatic and Aegean Seas, and the Levantine Basin (Sardà et al., 2004). The deep Mediterranean Sea is characterized by a trophic gradient that decreases from the western to the eastern basin (Danovaro et al., 2008b). This pattern reflects the different values of surface primary productivity: c. 163 ± 7 gC m−2 year−1 in the western Mediterranean and c. 121 ± 5 gC m−2 year−1 in the eastern Mediterranean (Bosc et al., 2004). Two bathyal plains (c. 700 km in diameter) have been identified at c. 1500 km distant from each other (one in the western Mediterranean and one in the eastern Mediterranean). These two plains are located within a very narrow bathymetric range (2760–2854 m depth), thus excluding the potential effects of hydrostatic pressure (which is nonetheless controlled as a covariable in statistical analyses). For each plain, a triangle of areas located c. 30 km apart was identified. In the western Mediterranean basin, for each of these three areas, three stations were also identified.
Hierarchical sampling strategy
The variability of deep-sea nematode biodiversity and the potential drivers was estimated at the following spatial scales: (1) the macroscale, between the western and eastern basins, at a distance of > 1500 km apart; (2) the mesoscale, among areas within the basins c. 30 km apart; (3) the local scale (only in the western Mediterranean Basin), among stations about 7 km apart; and (4) the small scale, with tens of metres between samples collected from independent deployments within each station (Fig. 1; Appendices S1 & S2 in Supporting Information). Considering the size of the ship and the potential drift during sampling, we estimate that the different deployments were of the order of tens of metres apart from each other, and were distributed randomly.
To account for temporal variability at the seasonal scale, replicated sediment samples for the analysis of nematode diversity and the available food sources were collected in two periods: April and November 2001, which can be considered as representative of spring and autumn, respectively, given the absence of short-term temporal fluctuations in environmental conditions at these depths (Stavrakakis et al., 2000; Heussner et al., 2006).
The laboratory procedures are summarized in Appendix S2. For each sampling site we determined the number of species present (species richness, as the sum of the number of species of three replicated samples) and the evenness of the nematode assemblages through Pielou's index (J′). To have a gross estimate of variability, we also estimated the maximum to minimum ratio of species richness at all spatial scales, from macroscale to small scale, in both basins. Since diversity indices are strongly influenced by the number of individuals identified, to standardize the values of nematode diversity and to facilitate comparisons with other studies, species-abundance data were converted into rarefaction diversity indices (Sanders, 1968; as modified by Hurlbert, 1971). The expected number of species for a theoretical sample of 51 nematode specimens, ES(51), was thus calculated (Soetaert & Heip, 1990; Danovaro et al., 2008a,b).
We measured turnover (beta) diversity to examine the changes in species composition at the different spatial scales, using the permdisp permutational multivariate dispersion analysis (Anderson et al., 2008). Prior to the analysis, the Bray–Curtis similarity matrix, which is based on species-abundance data (as presence/absence), was transformed into Euclidean distance by principal coordinates analysis. Beta diversity was measured as the multivariate dispersion from the group of the centroid (mean dispersion ± standard error). As permdisp cannot be applied for fewer than two replicates, simper analyses were used to estimate the dissimilarities in the species compositions at the small scale (among replicates) and to identify the presence of exclusive species at each sampling site. All of the diversity indices, including the turnover diversity, were calculated using the diverse, permdisp, pco and simper routines included in primer version 6+ software (Clarke & Gorley, 2006).
The functional diversity of the nematodes was estimated using the index of trophic diversity (ITD) as 1 – ITD, with ITD = g12 + g22 + g32 … + gn2, where according to (Wieser, 1953), g is the relative contribution of each trophic group to the total number of individuals and n is the number of trophic groups (Gambi et al., 2003). The nematodes were divided into four groups, as follows: 1A, selective (bacterial) deposit feeders; 1B, non-selective deposit feeders; 2A, epistrate feeders; and 2B, predators/omnivores. The value of 1 – ITD ranged from 0.00 (lowest diversity, where one trophic guild accounts for 100% of the nematode abundance) to 0.75 (highest trophic diversity, where four trophic guilds account for 25% each).
Potential food sources
The protocols for the analyses of the biochemical composition of the organic matter (chlorophyll a and phaeopigments, protein, carbohydrate, lipid) are reported in Appendix S2. As we hypothesized that the benthic biodiversity is dependent not only on the amount of trophic resources but also on the relative importance of the different resources, we calculated an index of resource evenness using the equation: index of resource diversity (IRD) = Σ(C protein/biopolymeric C)2 + (C carbohydrate/biopolymeric C)2 + (C lipid/biopolymeric C)2, based on the C equivalents of the protein, carbohydrate and lipid contents of the sediments and the biopolymeric carbon ratios, respectively. This index ranges from 0.33 (all of the biochemical components are equally represented in the biopolymeric C) to 1.0 (the biopolymeric C is theoretically made up of only one of the three components). In addition to the IRD as an indicator of the diversity of the food items, we also used the chlorophyll a to total phytopigment (Chla/Phyt) ratio and the protein to total phytopigment (Prt/Phyt) ratio, as indicators of the nutritional quality of the trophic resources. The Chla/Phyt ratio is indicative of the relative freshness of the organic detritus of algal origin that is deposited on the deep-sea floor, while the Prt/Phyt ratio is indicative of the availability of organic N for heterotrophic consumption.
We used regression models that are common to the spatial analysis of ecological data to evaluate the scales of variation of the abiotic variables and the diversity measures, and to quantify the degree of association between nematode diversity and the environment. The environmental variables (i.e. total phytopigments, biopolymeric C, IRD, Chla/Phyt and Prt/Phyt ratios) were standardized prior to the analysis. For each of these variables, we fitted a linear mixed effect (LME) model with macroscale, time and macroscale × time interactions as fixed terms and with mesoscale and local scale nested in mesoscale as random effects. We started with a full model fitted with restricted maximum likelihood (REML) to determine the optimal error structure. The full model included time as a covariate in the random part, to allow for possible time × mesoscale interactions. A series of reduced models was obtained by sequentially removing time, the local scale and finally the mesoscale from the random part of the model. The full and reduced models were compared sequentially through likelihood ratio tests. These tests also served to assess the significance of the variance components. Normalized residuals were extracted from the selected model and inspected for normality and variance homogeneity using quantile–quantile plots, and through plots of the residuals versus the fitted values. We then estimated the fixed coefficients and their standard errors through maximum likelihood. The data present maximum likelihood estimates for fixed effects and REML estimates for variance components.
To determine the importance of broad-scale variations in the environment, we also fitted a generalized additive model (GAM) to each abiotic variable, based on thin-plate splines of geographic coordinates, and we report the coefficient of determination to indicate the importance of broad-scale variation. This approach removes the broad-scale spatial structure, so the remaining variation in the residuals reflects the fine-scale variation and autocorrelation. We evaluated the importance of fine-scale variation through Moran's I on the GAM residuals, with lag distance determined from a semi-variogram of these residuals. The significance of Moran's I was determined from 999 permutations of the original observation for the given spatial weighting scheme.
LMEs were also used to examine the scales of variation in the nematode diversity [i.e. species richness, ES(51), evenness, index of trophic diversity], as described for the environmental variables. The potential importance of the environmental variables in determining changes in nematode diversity was evaluated through a comparison of the outcomes of the models that accounted for the spatial dependences at different scales, following the approach described by Lichstein et al. (2002). We started by fitting an OLS multiple regression model that included all of the environmental variables and time as covariates, with both large-scale spatial trends and fine-scale variations ignored. We then examined how these models changed when allowing for broad-scale spatial trends. This was achieved through GAMs that included the same covariates as the OSL regressions, but that modelled spatial trends through thin-plate splines of geographic coordinates. Finally, we evaluated how the OLS models change when accounting for fine-scale autocorrelation, which was assessed through conditional autoregressive (CAR) models. These models incorporate spatial autocorrelation using neighbourhood matrices that specify the relationships between the response variable in each sample and those in neighbouring samples. We chose an appropriate neighbourhood size for each response variable from semi-variograms of OLS residuals, and we compared the model fits for three distance–decay functions of spatial weights using the corrected Akaike information criterion (AICc): wij = 1, 1/distanceij and (1/distanceij)2; where wij is the weight that determines the relative influence of sample j on sample i. We selected wij = 1 for species richness and ES(51), and wij = 1/distanceij for evenness and functional diversity.
As our goal was to assess how much of the variation in the nematode diversity was accounted for by the different environmental variables and at what scale(s) these associations occurred, we omitted the categorical spatial variables (i.e. macroscale, mesoscale and local scale) from these models. Assumptions were evaluated for all of the models, as described in the analysis of the environmental data, and collinearity among covariates was assessed through the variance inflation factor (Fox & Monette, 1992).
To make the statistical tests more comparable among the OLS, GAM and CAR models, we assessed the significance of individual covariates through likelihood ratio tests for nested models, where a reduced model without a specific environmental covariate was compared with a full model that included all of the environmental predictors, as described in Lichstein et al. (2002). Thus, an environmental variable explains large-scale spatial variation in diversity if it is significant in the OLS regression but loses significance in GAM, which already accounts for broad-scale spatial structures. Similarly, an environmental variable explains small-scale spatial variation in diversity if it is significant in the OLS regression, but loses significance in CAR, which accounts for fine-scale spatial autocorrelation. Of course, some environmental variables can explain variations in nematode diversity at both small and large spatial scales. In this case, a covariate that is significant in the OLS regression should become non-significant both in GAM and CAR. Finally, covariates that are significant in the OLS regression can still be significant in GAM and/or CAR analyses. This suggests that the scales of variation accounted for by these analyses do not match that (those) of the environmental covariate(s). In this case, assessing the scale(s) of influence of the environmental variable independently from the outcomes of OLS, GAM and CAR, as we have done here, will aid in the interpretation of the data. Univariate analyses were performed in R2.11 (R Development Core Team, 2011).
Distance-based permutational multivariate analysis of variance (PERMANOVA; Anderson, 2001; McArdle & Anderson, 2001) was used to test for the presence of significant differences among nematode assemblages at different spatial scales, from macro- to meso- and local scales in spring and autumn (the local scale was only tested in the western basin). The analysis was based on Bray–Curtis dissimilarities that were calculated on presence/absence transformed data, and each term of the analysis was tested using 999 random permutations of the appropriate units (Anderson et al., 2008). The analysis consisted of four factors: macroscale, at two fixed levels (western and eastern basin); time, at two fixed levels (spring and autumn); mesoscale, at three random levels (area: A, B and C) nested in the macroscale; local scale (only for the western basin), at three random levels (station: 1, 2, 3), with n = 3 as the combination of factors. Pair-wise tests were carried out for the fixed factors of macroscale and time. All of the analyses were performed using primer version 6 (Clarke & Gorley, 2006), including the add-on PERMANOVA+ package (Anderson et al., 2008).
Finally, we assessed the linkages between the beta diversity and the environmental variables through semi-parametric multiple regression analysis based on Euclidean distances. This analysis was carried out using the routine distlm_forward.exe (Anderson, 2003), which allows the forward selection of the predictor variables using tests with permutation. P-values were obtained using 4999 permutations of raw data for the marginal tests (tests of individual variables), while for all of the conditional tests, the routine used 4999 permutations of residuals under a reduced model. To run this test, the following were considered as explanatory variables: depth, latitude, longitude, total phytopigments, biopolymeric C and IRD, Chla/Phyt and Prt/Phyt ratios as indicators of the diversity of food items and the quality of the trophic resources.
- Top of page
- Materials and Methods
- Supporting Information
Trophic characteristics of the sediments
There were significant macroscale × time interactions for the total phytopigments and biopolymeric C and Prt/Phyt ratio (Table 1). The total phytopigments and biopolymeric C concentrations were larger in the western Mediterranean than the eastern Mediterranean in spring, whereas the Prt/Phyt ratio followed the opposite pattern (Appendix S1). Hence, the differences in these abiotic variables at the macroscale varied considerably with season. GAMs confirmed the presence of significant broad-scale spatial variations in the total phytopigments and biopolymeric C, and also for the IRD, for which GAM on the geographic coordinates explained a significant fraction of variation (as indicated by the significant R2 in Table 1). Variance components highlighted significant variation at the local scale for the total phytopigments and Prt/Phyt ratio (Table 1). The residual variance was large for all of the abiotic variables, which indicates considerable variation at the small scale. None of the Moran's I tests were significant, which indicates that there is no fine-scale spatial autocorrelation in the abiotic variables. The variance at the mesoscale was negligible in all cases.
|Total phytopigments||Biopolymeric C||Index of resource diversity||Chlorophyll a/total phytopigments||Protein/total phytopigments|
|Macroscale × time||35.3***||28.7***||1.1||3.5||22.6***|
|R2 (from GAM)||0.15**||0.15**||0.17*||0.00||0.03|
Nematode species richness and evenness, and their potential drivers
Overall, 3562 nematodes were analysed and 182 species were identified, which belonged to 35 families and 127 genera. The logistic difficulties in determining the exact positioning of the multiple corer resulted in unintended systematic differences in depth between the basins. The samples in the western Mediterranean were slightly, but significantly, deeper than those in the eastern Mediterranean (average depths of 2852 m and 2786 m in the western and eastern basins, respectively; F1,4 = 3.5 × 104, P < 0.001). For this reason, we included depth as a covariate in all of the analyses of nematode diversity.
Nematode species richness was significantly greater in the western basin than the eastern basin, and this difference was greater in spring than autumn, which resulted in a significant macroscale × time interaction (Table 2, Fig. 2, Appendix S3). In contrast, there were no significant variations in species richness at the mesoscale and local scale, although there was a trend that suggested that the variance at the mesoscale was larger than zero (likelihood-ratio test = 3.53, 1 d.f., 0.05 < P < 0.07). Depth was significant in the OLS regression, but not in GAM, which confirmed macroscale differences in this variable. However, depth effects did not obscure the macroscale × time interaction in the analysis (Table 2, LME). The nematode species richness was positively associated with biopolymeric C and negatively related to IRD and the Prt/Phyt ratio. It should be noted that biopolymeric C was not significant in GAM, which is an indication of the potential effects of this variable on the broad-scale spatial variation in nematode richness. In contrast, IRD and the Prt/Phyt ratio retained significance in all of the analyses; thus, no specific scale of influence can be ascribed to these variables, although analysis of the data in Table 1 suggests that they should operate mostly at large and small scales, respectively.
|Source of variation|
|Intercept||10.52 (4.03)*||26.56 (1.01)***||27.99 (0.87)***||26.55 (1.02)***|
|Macroscale: western vs. eastern||24.00 (5.22)**|
|Time||6.44 (2.49)*||1.52 (1.67)||0.24 (1.43)||1.42 (1.55)|
|Macroscale × time||−11.49 (2.96)***|
|Depth||0.71 (2.28)||6.42 (0.82)***||−1.43 (1.78)||6.30 (0.85)***|
|Total phytopigments||−0.35 (1.11)||−0.98 (0.94)||−1.45 (1.04)|
|Biopolymeric carbon||4.72 (1.01)***||3.79 (0.87)||5.65 (0.94)***|
|Index of resource diversity||−1.56 (0.83)*||−0.70 (0.71)*||−1.58 (0.76)*|
|Chlorophyll a/total phytopigments||1.12 (0.76)||1.00 (0.65)||0.56 (0.66)|
|Proteins/total phytopigments||−2.02 (0.84)*||−2.73 (0.72)***||−2.14 (0.77)**|
The results for ES(51) were very similar to those of species richness, although in this case there was significant variation also at the mesoscale (Appendices S3 & S4).
The western Mediterranean had larger evenness than the eastern Mediterranean, and this difference was greater in spring than autumn, which results in a significant macroscale × time interaction (Table 3, Appendix S3). Evenness also showed large and significant variation at the mesoscale, but not at the local scale. The macroscale × time interaction persisted after allowing for depth effects (LME analysis), the latter being significant in OLS and CAR. Evenness was positively associated with biopolymeric C and negatively related to the Prt/Phyt ratio. These environmental variables accounted for the large-scale spatial variation in evenness, although neither GAM nor CAR analyses captured their spatial structure adequately.
|Source of variation|
|Intercept||0.44 (0.06)***||0.73 (0.01)***||0.74 (0.01)***||0.74 (0.01)***|
|Macroscale: western vs. eastern||0.43 (0.08)***|
|Time||0.08 (0.03)**||−0.02 (0.02)||−0.04 (0.02)**||−0.03 (0.02)|
|Macroscale × time||−0.22 (0.03)***|
|Depth||0.03 (0.03)||0.13 (0.01)***||0.001 (0.04)||0.13 (0.01)***|
|Total phytopigments||0.004 (0.02)||−0.003 (0.01)||−0.02 (0.01)|
|Biopolymeric carbon||0.06 (0.01)***||0.04 (0.01)***||0.08 (0.01)*|
|Index of resource diversity||−0.01 (0.01)||0.004 (0.01)||−0.01 (0.01)|
|Chlorophyll a/total phytopigments||0.002 (0.01)||0.001 (0.01)||−0.01 (0.01)|
|Proteins/total phytopigments||−0.04 (0.01)***||−0.05 (0.008)***||−0.04 (0.01)***|
|S2mesoscale||2.3 × 10-3***|
|S2local||8.4 × 10-4|
|S2residuals||3.7 × 10-3|
Nematode species composition and turnover (beta) diversity
Only 27 families, 46 genera and 56 species were observed in both of the basins, whereas 73 genera and 119 species, and 5 genera and 6 species, were exclusively reported for the western and the eastern basin, respectively. In both basins the most abundant families (representing > 10% of the total nematode abundance) were Oxystominidae (14%), Chromadoridae (12%) and Xyalidae (12%). The families Draconematidae, Ethomolaimidae, Haliplectidae, Pandolaimidae, Paramicrolaimidae, Siphonolaimidae and Trefusidae were exclusively observed in the western Mediterranean, whereas only the family Lauratonematidae was exclusive to the eastern Mediterranean. The dominant nematode species differed between the two basins: Halalaimus sp4 (7%), Amphymonhystrella sp1 (5%) and Syringolaimus sp1 (4%) in the western Mediterranean, and Viscosia sp1 (21%), Halalaimus sp4 (10%) and Syringolaimus sp1 (6%) in the eastern Mediterranean. The permdisp results revealed that the beta diversity was significantly higher at the macroscale (average dispersion 44.3 ± 3.1, t-test P = 0.01) than the mesoscale (average dispersion 39.1 ± 1.6 for the western basin; average dispersion 36.5 ± 3.2 for the eastern basin) which, in turn, was significantly higher than the local scale (average dispersion 33.5 ± 1.1, t-test P = 0.001) (Fig. 2). The high species dispersion was already evident from the preliminary analysis of the taxonomic composition of nematode assemblages, with the presence of exclusive nematode species (and even exclusive families) inhabiting each basin, sampling area and station. Since permdisp is not applicable for the small scale, simper analyses was used, which revealed the presence of high variability in species composition also among the replicates (percentage of dissimilarity, from 29 to 72% for the western basin, and from 40 to 100% for the eastern basin). The results of PERMANOVA showed significant interactions for macroscale × time and mesoscale × time, while there were no differences among nematode assemblages at the local scale (Table 4). The pairwise tests revealed significant differences in nematode species composition at the macroscale in both sampling periods (P = 0.001 and P = 0.003 in spring and autumn, respectively), and significant differences between spring and autumn (P = 0.029) only in the western basin.
|Source||Nematode species composition|
|d.f.||MS||P||% explained variance|
|Macroscale × time||1||7505.1||*|
|Local [mesoscale (macroscale)]||6||1881.5||n.s.||4|
|Time × mesoscale (macroscale)||4||3541.7||**||16|
|Time × local [mesoscale (macroscale)]||4||1811.8||n.s.||5|
Functional diversity and its potential drivers
Functional diversity, as 1 – ITD, was positively related to the species richness in both basins (Appendix S5). The trophic diversity index was larger in the western Mediterranean than the eastern Mediterranean in spring (Appendix S3), whereas the opposite pattern was observed in autumn, which resulted in a significant macroscale × time interaction (Table 5). This index did not vary at the mesoscale or local scales, and showed no significant relationships with any of the environmental covariates, apart from depth, which nevertheless did not obscure the macroscale effects (LME analysis).
|Source of variation|
|Intercept||0.40 (0.04)***||0.38 (0.01)***||0.38 (0.01)***||0.38 (0.01)***|
|Macroscale: western vs. eastern||−0.01 (0.06)|
|Time||−0.12 (0.03)***||−0.042 (0.02)*||−0.04 (0.02)||−0.04 (0.02)*|
|Macroscale × time||0.11 (0.04)**|
|Depth||−0.05 (0.02)||−0.02 (0.01)*||−0.03 (0.03)||−0.02 (0.010)*|
|Total phytopigments||−0.004 (0.014)||−0.01 (0.01)||−0.00 (0.01)|
|Biopolymeric carbon||−0.01 (0.01)||−0.01 (0.01)||−0.01 (0.01)|
|Index of resource diversity||0.00 (0.01)||−0.00 (0.01)||−0.00 (0.01)|
|Chlorophyll a/total phytopigments||−0.01 (0.01)||−0.01 (0.01)||−0.01 (0.01)|
|Proteins/total phytopigments||0.01 (0.01)||0.01 (0.01)||0.01 (0.01)|
|S2residuals||4.2 × 10-3|
To further characterize the functional diversity in the nematode assemblages, we also examined the patterns of variation in the abundance of the four trophic guilds (Appendices S6–S9). Selective deposit and epistrate feeders were more abundant in the western basin than the eastern basin, and this difference was greater in spring than autumn; this resulted in a significant macroscale × time interaction, while non-selective deposit feeders were also more abundant in the western basin, consistently in both sampling periods. The abundance of predators was similar between the basins, and declined slightly between spring and autumn. The differences between the basins at the macroscale persisted after accounting for depth effects (LME analysis), which were significant for all of the trophic guilds except the predators. Similarly, all of the trophic guilds except the predators were positively associated with biopolymeric C, whilst epistrate feeders were also negatively associated with IRD. These environmental variables accounted for large-scale spatial variations in the nematode trophic guilds, although neither GAM nor CAR analyses captured their spatial structure adequately.
- Top of page
- Materials and Methods
- Supporting Information
Spatial variability of nematode diversity
Early quantitative investigations on biodiversity conducted at large spatial scales have shown that deep-sea ecosystems are not, as previously hypothesized, biological deserts; rather, they are among the most diverse systems on the globe, with values of expected species numbers comparable to, and second only to, coastal tropical systems (Sanders & Hessler, 1969; Grassle & Maciolek, 1992). This is probably also true for the deep Mediterranean Sea (Ramirez-Llodra et al., 2010; Coll et al., 2012). Indeed, although the biodiversity of the macrofauna and megafauna in the deep Mediterranean Sea is apparently lower than that in other deep-sea regions (Danovaro et al., 2010), we show here that the nematode diversity is comparable to values reported world-wide (Fig. 3). Despite the low abundance of individuals, nematode diversity, as ES(51), is also high in the sediments of the deep Mediterranean Sea. Comparing the biodiversity at depths ranging from c. 200 to 5000 m, the values reported at the shelf break are no different from those reported along the slope or at abyssal depths. Our findings show that the data from the deep western Mediterranean and eastern Mediterranean at 3000 m in depth cover the widest ranges of biodiversity that have been reported in the literature for deep-sea ecosystems world-wide. This suggests that the differences observed for nematode fauna among oceanic regions are more important than the bathymetric gradients. It is now evident that high values of biodiversity (ES(n), with n varying from 51 to 100 depending on the taxon and the study; Danovaro et al., 2010) characterize most of the deep-sea regions world-wide. However, the available information on the combined spatial and temporal variability of deep-sea biodiversity is very scant. Our data indicate that the variability in biodiversity (as species richness, ES(51), and evenness) is largest at the macroscale, while the largest maximum to minimum ratio of species richness is observed in the eastern Mediterranean at both the small scale and mesoscale (Fig. 4a). The maximum to minimum ratio of species richness reported here for the small scale is similar to, or even higher than, several other deep-sea regions, at both deeper and shallower depths (Fig. 4b). These findings are based on a dataset that was obtained using the same, or similarly performing, sampling devices and conducted in the same laboratory by intercalibrated operators; these suggest that deep-sea environments share similar ranges of biodiversity variability (the maximum to minimum ratios ranged from 10 to 50% at all scales in the Mediterranean Sea), with the average value of the maximum to minimum ratio of species richness at the small scale of 1.3 ± 0.2. For the first time, our data enable the assessment of the confidence level of the maximum to minimum ratio in extrapolating data based on analyses from small to large spatial scales (e.g. mesoscale), and they reveal that this value is consistent at all of the investigated spatial scales in the deep Mediterranean Sea, and is similar to that reported at the small scale world-wide. We report also that, on average, the differences observed in terms of the species richness at the macroscale (western to eastern species richness ratio = 3) are lower than those reported for both total meiofaunal and nematode abundance (western to eastern abundance ratio = 5, faunal abundance from Gambi & Danovaro, 2006), which suggests different responses of the abundance and diversity to environmental/ trophic changes that occur at the macroscale.
We also found that species richness increased moving westwards, although the ratio between the western basin and the eastern basin is about two- to three-fold lower than that shown by the abundance. These data allow us to hypothesize that the observed differences in the nematode abundance at the macroscale are in a large part due to the different recruitment success of the species that inhabit the two basins, rather than to their different ingression from adjacent regions (i.e. from the Atlantic Ocean, through the Gibraltar Strait for the western basin, and from the Black Sea and Red Sea for the eastern basin). This implies that differences in availability of food sources at the macroscale are more relevant in the control of the abundance than the species richness.
At the same time, both species richness, as ES(51), and evenness showed significant spatial variability also at the mesoscale, which suggests that in regions characterized by similar trophic status the heterogeneity of the topographic and environmental characteristics has importance in determining the high variability in the biodiversity and evenness. We can thus conclude that the spatial variability of biodiversity at the macroscale is controlled by different processes from those acting at smaller spatial scales (see below for further discussion).
As reported for species richness, the values of turnover (beta) diversity in the deep Mediterranean Sea are also typically high at all of the spatial scales, and the highest source of variability is encountered at the macroscale and mesoscale. These findings are supported by the data from the random subsampling in the western basin, which avoids any bias for the spatial distribution of the species richness and beta diversity due to the different sampling efforts carried out in the two basins (Appendix S10).
The beta diversity decreases with the decrease in spatial scale, especially in the western basin, although the variability in species composition still remains relatively high at the smallest spatial scale (tens of metres). Similar results have been reported recently from the deep Arctic Sea, where, however, pseudoreplicates were considered (Gallucci et al., 2009). Altogether these data led us to hypothesize that the processes of nematode species aggregation at small spatial scales (less than a few metres) has a key role in influencing/driving the variations in species composition within deep-sea nematode assemblages at all spatial scales. Consistent with what has been observed for terrestrial ecosystems (Huston, 1999), these findings support the hypothesis that in the deep sea also the species interactions are important in setting the changes in species composition (beta diversity) at the smaller spatial scales, and they contribute to the effects determined by other scale-dependent factors (such as, among others, habitat heterogeneity at the smallest scale).
The data presented here suggest that species richness and beta diversity have opposite patterns in the deep Mediterranean Sea: species richness is significantly greater in the western Mediterranean than the eastern Mediterranean, whereas beta diversity is higher within the eastern Mediterranean than the western Mediterranean. These patterns might be the result of the effects of different environmental characteristics (topography and trophic conditions), the history and environmental events (episodic events and climate change, with different spatial extension and intensity) that characterize these two basins (Danovaro et al., 2004, 2008b; Canals et al., 2006; Gambi & Danovaro, 2006; Pusceddu et al., 2010, 2013). All of these environmental factors probably have different effects on the biodiversity attributes in the western and eastern Mediterranean basins. The functional diversity in the deep Mediterranean Sea shows significant spatial variability at the macroscale, especially in spring, when the values of the trophic diversity index are significantly lower in the eastern than the western Mediterranean. This is the result of significant variability at the macroscale of the abundance of all of the nematode trophic groups except for the predators. The larger skewness of the functional diversity of the nematode assemblages that inhabit the eastern Mediterranean basin is associated with a higher percentage of predators, and in particular the genus Viscosia, which dominates the nematode assemblages in spring (Appendix S11). This is also confirmed by the simper analyses, and these findings suggest that the quantitative importance of predators is a consistent and typical feature of the deep-sea nematode assemblages of the eastern Mediterranean Sea (Danovaro et al., 2008b). These percentages of predators are the highest reported so far in deep-sea investigations (Soetaert & Heip, 1995; Gambi et al., 2003), and this led us to hypothesize a key role for this trophic group that can influence the relationship between biodiversity and ecosystem functioning in these systems, and which deserves further investigation.
The spatial patterns in nematode functional diversity agree well with those reported for species richness, but not with those of beta diversity. This is surprising, as changes in species composition of nematode assemblages might be related to changes in functional diversity, as different species have different functional traits (i.e. they belong to different trophic groups). The variability of functional diversity might conceivably imply differences in ecological interactions among the trophic levels, with consequences for the structure and functioning of the communities (Giere, 2009) and, consequently, for the relationships between biodiversity and ecosystem functioning in deep-sea ecosystems (Danovaro et al., 2008a). On the other hand, any changes in community composition – and thus in beta diversity – might be associated with changes in the structure and functioning of the benthic food webs, and therefore of the functional diversity.
Previous studies have hypothesized a rapid response (i.e. days to weeks) of deep-sea fauna to temporal variability in the supply of food inputs, not only in terms of abundance and biomass but also in terms of biodiversity (Danovaro et al., 2004; Smith et al., 2008; Gooday et al., 2010; McClain & Barry, 2010). The data from the present study reveal that the variations at both the macroscale and mesoscale in species richness, evenness, composition and functional diversity are larger in spring than in autumn, which suggests that the food inputs reaching the sea floor as a result of the enhanced productivity processes that occur in the euphotic zone in spring have a significant impact upon, and indeed increase, all of the attributes of deep-sea biodiversity.
Factors controlling the spatial patterns of biodiversity
Previous investigations have revealed the important role of available energy in controlling the spatial distribution of biodiversity at the large spatial scale in deep-sea ecosystems (Levin et al., 2001; Lambshead et al., 2002; Snelgrove & Smith, 2003; Rex et al., 2005; Smith et al., 2008; Pusceddu et al., 2009; Rex & Etter, 2010; McClain et al., 2012; Brault et al., 2013a). Our analyses emphasize the importance of the quantity of food sources (i.e. biopolymeric C) as a driver of spatial variability in nematode species richness and evenness at the macroscale and mesoscale. We also report that total phytopigments, the food quality (Prt/Phyt and Chla/Phyt ratios) and the diversification of the food sources have key roles, and these explain statistically up to 100% of the biodiversity variations at larger spatial scales (especially for beta diversity; Table 6). The total phytopigments include chlorophyll a and phaeopigments (the degradation products of chlorophylls). Therefore, the Chla/Phyt ratio represents an estimate of the freshness of the algal material that is deposited on the deep-sea floor, whereas the Prt/Phyt ratio is an estimate of the relative importance of the organic material of a detrital/heterotrophic nature versus organic material associated with algal detritus (Pusceddu et al., 2009). We show that the nematode species richness and evenness are negatively related to the Prt/Phyt ratio, while the total phytopigments and Chla/Phyt ratio explain large fractions of the beta diversity variation at the macroscale and mesoscale. These findings suggest that the quality (and freshness) of the organic inputs supplied from the water column drive the species composition. Conversely, large inputs of aged detritus of heterotrophic origin, with lower nutritional quality, were associated with lower species richness and evenness. Recent studies based on linear inverse modelling (LIM) exercises have postulated a limited role of labile detritus (i.e. phytopigments) in explaining the functioning of benthic trophic webs along several continental margins and deep-sea plains (Van Oevelen et al., 2012). The same simulations have postulated that the functioning of deep-sea benthic trophic webs is mainly dependent upon the availability of semi-labile detritus (i.e. the biopolymeric C; sensu Pusceddu et al., 2009). Our data allow the identification of the pivotal role of biopolymeric C in controlling also the deep-sea biodiversity at a depth of 3000 m, while the availability and freshness of the sedimentary organic matter (i.e. phytopigments) have key roles in driving nematode beta diversity.
|Spatial scale||Season||Explanatory variable||F||P||Var(%)||Cum(%)|
|Mesoscale: western basin||Spring||IRD||966.7||***||92||92|
|Mesoscale: eastern basin||Spring||Prt/Phyt||2742.6||**||68||68|
|Local scale: western Mediterranean||Spring||Depth||509.4||*||54||54|
|Small scale: western Mediterranean||Spring||Depth||1522.9||***||42||42|
|Small scale: eastern Mediterranean||Spring||Prt/Phyt||2500.7||*||62||62|
When the analysis is performed at local and small scales, the proportion of variation in beta diversity explained by the quality and composition of the food sources decreases to a large extent (Table 6). These data indicate that at smaller scales drivers such as species interactions and habitat heterogeneity are also important, as well as the availability of food. Our data also reveal that the sampling depth explains some of the variations in the biodiversity at all of the spatial scales, although the effects of this covariate are not robust enough to obscure the macroscale patterns observed. Overall, these data provide new insights into the scales and the processes driving the spatial and temporal variability of biodiversity in the deep sea.
Also in light of the episodic events that can dramatically change the transport and distribution of resources from the upper water column to the deep sea (Smith et al., 2009), global changes are expected to influence the quantity, quality and distribution of the food supply to the deep-sea benthos (Danovaro et al., 2004; Coma et al., 2009; Pusceddu et al., 2010, 2013). Since these variables are crucial in the determination of the variability of the biodiversity distribution, based on the results of our investigation, we can anticipate that global changes will have a significant impact on the distribution of species richness, as well as on the beta and functional diversity of the deep-sea fauna.
- Top of page
- Materials and Methods
- Supporting Information
This study was carried out within the framework of the ADIOS and Hotspot Ecosystem Research and Man's Impact on European Seas (HERMIONE, contract no. 226354) projects, which are financially supported by the Europe Commission, and by the OBAMA project, which is supported by the Italian Ministry for Education, Universities and Research (MIUR), and The Italian Research for the Sea, Flagship Project RITMARE (coordinated by the Italian National Research Council) funded by MIUR within the National Research Programme 2011–2013.
- Top of page
- Materials and Methods
- Supporting Information
- 2001) A new method for non-parametric multivariate analysis of variance. Austral Ecology, 26, 32–46. (
- 2003) DISTLM forward: a FORTRAN computer program to calculate a distance-based multivariate analysis for a linear model using forward selection. Department of Statistics, University of Auckland, Auckland, New Zealand. (
- 2008) PERMANOVA+ for PRIMER: guide to software and statistical methods. PRIMER-E, Plymouth, UK. , & (
- 2010) Regression analysis of spatial data. Ecology Letters, 13, 246–264. , , , & (
- 2010) Deep-water corals promote higher beta diversity in deep-sea meiofaunal assemblages along continental margins. Biological Conservation, 143, 1687–1700. , , , , & (
- 2004) Seasonal and interannual variability in algal biomass and primary production in the Mediterranean Sea, as derived from 4 years of SeaWiFS observations. Global Biogeochemical Cycles, 18, GB1005, doi:10.1029/2003GB002034. , & (
- 2013a) Geographic evidence for source-sink dynamics in deep-sea gastropods of the eastern North Atlantic: an approach using nested analysis. Global Ecology and Biogeography, 22, 433–439. , , & (
- 2013b) Contrasting patterns of alpha and beta diversity in deep-sea bivalves of the Eastern and Western North Atlantic. Deep-Sea Research Part II, 92, 157–164. , , , , & (
- 2006) Flushing submarine canyons. Nature, 444, 354–357. , , , , & (
- 2002) Spatial scale dictates the productivity–biodiversity relationship. Nature, 416, 427–430. & (
- 2006) PRIMER v6: user manual/tutorial. PRIMER-E, Plymouth, UK. & (
- 2012) The Mediterranean Sea under siege: spatial overlap between marine biodiversity, cumulative threats and marine reserves. Global Ecology and Biogeography, 21, 465–480. , , , , , , , , , , , , , & (
- 2009) Global warming-enhanced stratification and mass mortality events in the Mediterranean. Proceedings of the National Academy of Sciences USA, 106, 6176–6181. , , , , & (
- 2010) A census of marine biodiversity knowledge, resources, and future challenges. PLoS ONE, 5( 8), e12110. doi: 10.1371/journal.pone.0012110. , , , , & (
- 2001) Biodiversity may regulate the temporal variability of ecological systems. Ecology Letters, 4, 72–85. , & (
- 2004) Biodiversity response to climate change in a warm deep sea. Ecology Letters, 7, 821–828. , & (
- 2008a) Exponential decline of deep-sea ecosystem functioning linked to benthic biodiversity loss. Current Biology, 18, 1–8. , , , , , , & (
- 2008b) Deep-sea biodiversity in the Mediterranean Basin: testing for longitudinal, bathymetric and energetic gradients. Ecography, 31, 231–244. , , & (
- 2009) α-, β-, γ-, δ and ε-diversity of deep-sea nematodes in canyons and open slopes of the Northeast Atlantic and Mediterranean margins. Marine Ecology Progress Series, 396, 197–209. , , , & (
- 2010) Deep-sea biodiversity in the Mediterranean Sea: the known, the unknown, and the unknowable. PLoS ONE, 5(8), e11832. doi:10.1371/journal.pone.0011832 , , , , , , , , , , , , , , , & (
- 1995) Marine benthos hypoxia: a review of its ecological effects and the behavioural responses of benthic macrofauna. Oceanography and Marine Biology: Annual Review, 33, 245–303. & (
- 1992) Patterns of species diversity in the deep sea as a function of sediment particle size diversity. Nature, 369, 576–578. & (
- 1992) Generalized collinearity diagnostics. Journal of the American Statistical Association, 87, 178–183. & (
- 2005) Patterns of distribution of marine assemblages from rocky shores: evidence of relevant scales of variation. Marine Ecology Progress Series, 296, 13–29. , & (
- 2008) How many habitats are there in the sea (and where)? Journal of Experimental Marine Biology and Ecology, 366, 109–115. , & (
- 2009) Small-scale spatial patterns of meiobenthos in the Arctic deep sea. Marine Biodiversity, 39, 9–25. , & (
- 2006) A multiple-scale analysis of metazoan meiofaunal distribution in the deep Mediterranean Sea. Deep-Sea Research I, 53, 1117–1134. & (
- 2003) Biodiversity of nematode assemblages from deep-sea sediments of the Atacama Slope and Trench (South Pacific Ocean). Deep-Sea Research I, 50, 103–117. , & (
- 2010) Latitudinal, longitudinal and bathymetric patterns of abundance, biomass of metazoan meiofauna: importance of the rare taxa and anomalies in the deep Mediterranean Sea. Advances in Oceanography and Limnology, 1, 1, 167–197. , & (
- 2000) Global patterns in biodiversity. Nature, 405, 220–227. (
- 2009) Meiobenthology. The microscopic motile fauna of aquatic sediments, p. 527. Springer-Verlag, Berlin. (
- 1998) Deep-sea benthic foraminiferal diversity in the NE Atlantic and NW Arabian Sea: a synthesis. Deep-Sea Research Part II, 45, 165–201. , , & (
- 2010) Decadal-scale changes in shallow-infaunal foraminiferal assemblages at the Porcupine Abyssal Plain, NE Atlantic. Deep-Sea Research Part II, 57, 1362–1382. , , & (
- 1992) Deep-sea species richness: regional and local diversity estimates from quantitative bottom samples. The American Naturalist, 139, 313–341. & (
- 2006) Spatial and temporal variability of downward particle fluxes on a continental slope: lessons from an 8-yr experiment in the Gulf of Lions (NW Mediterranean). Marine Geology, 234, 63–92. , , , , , & (
- 1971) The non-concept of species diversity: a critique and alternative parameters. Ecology, 52, 577–586. (
- 1999) Local processes and regional patterns: appropriate scales for understanding variation in the diversity of plants and animals. Oikos, 86, 393–401. (
- 1976) Deep-sea species diversity : does it have a characteristic scale? Journal of Marine Research, 34, 217–245. (
- 2004) Marine nematode biodiversity. Nematology: advances and perspectives Vol 1: nematode morphology, physiology and ecology (ed. by Z.X. Chen, S.Y. Chen and D.W. Dickson), pp. 436–467. CABI Publishing, Wallingford, UK. (
- 2001) The impact of large-scale natural physical disturbance on the diversity of deep-sea North Atlantic nematodes. Marine Ecology Progress Series, 214, 121–126. , , , , & (
- 2002) Latitudinal diversity patterns of deep-sea marine nematodes and organic fluxes: a test from the central equatorial Pacific. Marine Ecology Progress Series, 236, 129–135. , , , , , & (
- 2010) The sustained observatory over the Porcupine Abyssal Plain (PAP): insights from time series observations and process studies. Deep-Sea Research Part II, 57, 1267–1271. , & (
- 1993) Spatial autocorrelation – trouble or a new paradigm? Ecology, 74, 1659–1673. (
- 2001) Environmental influences on regional deep-sea species diversity. Annual Review of Ecology and Systematics, 32, 51–93. , , , , , , , & (
- 2002) Spatial autocorrelation and autoregressive models in ecology. Ecological Monographs, 72, 445–463. , , & (
- 2001) Fitting multivariate models to community data: a comment on distance-based redundancy analysis. Ecology, 82, 290–297. & (
- 2010) Habitat heterogeneity, disturbance, and productivity work in concert to regulate biodiversity in deep submarine canyons. Ecology, 91, 964–976. & (
- 2012) Energetics of life on the deep seafloor. Proceedings of the National Academy of Sciences USA, 109, 15366–15371. , , & (
- 2009) Quantity and bioavailability of sediment organic matter as signatures of benthic trophic status. Marine Ecology Progress Series, 375, 41–52. , , & (
- 2010) Ecosystem effects of dense water formation on deep Mediterranean Sea ecosystems: an overview. Advances in Oceanography and Limnology, 1, 51–62. , , , , , , , , , , , & (
- 2013) Major consequences of an intense dense shelf water cascading event on deep-sea benthic trophic conditions and meiofaunal biodiversity. Biogeosciences, 10, 2659–2670. , , , , , , , , , & (
- R Development Core Team (2011) R: a language and environment for statistical computing. R Foundation for Statistical Computing, Vienna, Austria.
- 2010) Deep, diverse and definitely different: unique attributes of the world's largest ecosystem. Biogeosciences, 7, 2851–2899. , , , et al. (
- 2010) Deep-sea biodiversity: pattern and scale. Harvard University Press, Cambridge, MA. & (
- 2005) Large-scale biogeographic patterns in marine molluscs: a confluence of history and productivity? Ecology, 86, 2288–2297. , , & (
- 1968) Marine benthic diversity: a comparative study. The American Naturalist, 102, 243–282. (
- 1969) Ecology of deep-sea benthos. Science, 163, 1419–1424. & (
- 2004) An introduction to Mediterranean deep-sea biology. Scientia Marina, 68, 3, 7–38. , , , , , & (
- 2008) Abyssal food limitation, ecosystem structure and climate change. Trends in Ecology and Evolution, 23, 518–528. , , , & (
- 2009) Climate, carbon cycling, and deep-ocean ecosystems. Proceedings of the National Academy of Sciences USA, 106, 19211–19218. , , , , & (
- 2003) A riot of species in an environmental calm: the paradox of the species-rich deep-sea floor. Oceanography and Marine Biology: Annual Review, 40, 311–342. & (
- 1990) Sample-size dependence of diversity indices and the determination of sufficient sample size in a high-diversity deep-sea environment. Marine Ecology Progress Series, 59, 305–307. & (
- 1995) Nematode assemblages of deep-sea and shelf break sites in the North Atlantic and Mediterranean Sea. Marine Ecology Progress Series, 125, 171–183. & (
- 2000) Downward fluxes of settling particles in the deep Cretan Sea (NE Mediterranean). Progress in Oceanography, 46, 217–240. , , , , & (
- 2003) Large-scale spatial and temporal patterns of deep-sea benthic species diversity. Ecosystems of the deep Oceans (ed. by P.A. Tyler), pp. 295–312. Elsevier, Amsterdam. , & (
- 2010) Global patterns and predictors of marine biodiversity across taxa. Nature, 466, 1098–1101. , , , , , & (
- 2011) Species–energy relationships in deep-sea molluscs. Biology Letters, 7, 718–722. , , , & (
- 2012) Carbon flows in the benthic food web of the Porcupine Abyssal Plain: the (un)importance of labile detritus in supporting microbial and faunal carbon demands. Limnology and Oceanography, 57, 645–664. , & (
- 2010) The contribution of deep-sea macrohabitat heterogeneity to global nematode diversity. Marine Ecology: An Evolutionary Perspective, 31, 1, 6–20. , , , et al. (
- 2010) Bathymetric zonation of deep-sea macrofauna in relation to export of surface phytoplankton production. Marine Ecology Progress Series, 399, 1–14. , , , , , , , , , , & (
- 1953) Die Beziehung zwischen Mundhöhlengestalt, Ernährungsweise und Vorkommen bei freilebenden marinen Nematoden. Arkiv for Zoologi, 2–4, 439–484. (
- 2012) Pockmarks enhance deep-sea benthic biodiversity: a case study in the western Mediterranean Sea. Diversity and Distributions, 18, 832–846. , & (
The Marine Biology research team of the Department of Life and Environmental Sciences of the Polytechnic University of Marche includes a highly interdisciplinary and multidisciplinary group of scientists who are devoted to the investigation of marine biology and ecology, with a special focus on the understanding of the links between biodiversity and ecosystem functioning, and of the management and protection of deep-sea habitats.
Cristina Gambi works in the Department of Life and Environmental Sciences of the Polytechnic University of Marche, in Italy. Her research interests are focused on deep-sea ecology, with a special focus on the understanding of the patterns of biodiversity at large spatial scales, and of the relationships between biodiversity and ecosystem functioning in deep-sea ecosystems.
Author contributions: R.D. and C.G. conceived the idea; C.G. and R.D. collected the data; C.G., A.P. and L.B.-C. analysed the data; C.G. and R.D. led the writing of the manuscript, and all of the other authors contributed with suggestions and corrections. All of the authors contributed to finalizing of the manuscript.
- Top of page
- Materials and Methods
- Supporting Information
Appendix S1 Sampling sites and potential food sources in the deep western and eastern Mediterranean Sea.
Appendix S2 Details on sampling activities, laboratory procedures for the analysis of nematode diversity and potential food sources.
Appendix S3 Deep-sea benthic biodiversity in the Mediterranean Sea at different spatial scales.
Appendix S4 Regression coefficients (and standard error) of linear mixed effect (LME), ordinary least squares (OLS), generalized additive (GAM) and conditional autoregressive (CAR) models of standardized nematode species richness as ES(51).
Appendix S5 The relationship between expected species number, ES(51), and functional diversity in the western and eastern Mediterranean Sea.
Appendix S6 Regression coefficients (and standard error) of linear mixed effect (LME), ordinary least squares (OLS), generalized additive (GAM) and conditional autoregressive (CAR) models of nematode (bacterial) selective deposit feeders.
Appendix S7 Regression coefficients (and standard error) of linear mixed effect (LME), ordinary least squares (OLS), generalized additive (GAM) and conditional autoregressive (CAR) models of nematode non-selective deposit feeders.
Appendix S8 Regression coefficients (and standard error) of linear mixed effect (LME), ordinary least squares (OLS), generalized additive (GAM) and conditional autoregressive (CAR) models of nematode epistrate feeders.
Appendix S9 Regression coefficients (and standard error) of linear mixed effect (LME), ordinary least squares (OLS), generalized additive (GAM) and conditional autoregressive (CAR) models of nematode predators/omnivores.
Appendix S10 The importance of the sampling effort.
Appendix S11 Nematode trophic structure in the Mediterranean Sea at different spatial scales.
Please note: Wiley Blackwell is not responsible for the content or functionality of any supporting information supplied by the authors. Any queries (other than missing content) should be directed to the corresponding author for the article.