Temporal stability of European rocky shore assemblages: variation across a latitudinal gradient and the role of habitat-formers

Download (0)

Full text

(1)

Temporal stability of European rocky shore assemblages: variation across a latitudinal gradient and the role of habitat-formers

F. Bulleri, L. Benedetti-Cecchi, M. Cusson, E. Maggi, F. Arenas, R. Aspden, I. Bertocci, T. P. Crowe, D. Davoult, B. K. Eriksson, S. Fraschetti, C. Golléty, J. N. Griffin, S. R. Jenkins, J. Kotta,

P. Kraufvelin, M. Molis, I. Sousa Pinto, A. Terlizzi, N. Valdivia and D. M. Paterson

F. Bulleri (fbulleri@biologia.unipi.it), Dipto di Scienze Botaniche. Ecologiche e Geologiche, Univ. di Sassari, Via Piandanna 4, IT-0071 Sassari, Italy. – FB, L. Benedetti-Cecchi, M. Cusson, E. Maggi, I. Bertocci, Dipto di Biologia, Univ. di Pisa, CoNISMa, Via Derna 1, IT-56126, Pisa, Italy. MC also at: Dépt des sciences fondamentales, Univ. du Québec à Chicoutimi, 555 Boulevard de l’Université, Chicoutimi, QC, G7H 2B1 Canada. – T. P. Crowe, School of Biology and Environmental Science, Univ. College Dublin, Belfield, Dublin 4, Ireland.

– IB and F. Arenas, Laboratory of Coastal Biodiversity, Centre of Marine and Environmental Research (CIIMAR), Univ. of Porto, Rua dos Bragas 289, PT-4050-123 Porto, Portugal. – R. Aspden, C. Golléty and D. M. Paterson, Scottish Oceans Inst., Univ. St Andrews, St Andrews, Fife, KY16 8LB, UK. – CG and D. Davoult, UPMC Univ Paris 06, UMR 7144, Station Biologique de Roscoff, FR-29682 Roscoff, France.

– B. K. Eriksson, Dept of Marine Benthic Ecology and Evolution, Centre for Ecological and Evolutionary Studies, Univ. of Groningen, Nijenborgh 7, NL-9747 AG Groningen, the Netherlands. – S. Fraschetti and A. Terlizzi, Dipto di Scienze e Tecnologie Biologiche ed Ambientali, Univ. del Salento, CoNISMa, IT-73100 Lecce, Italy. – J. N. Griffin and S. R. Jenkins, Marine Biological Ass., Citadel Hill, Plymouth, PL1 2PB, UK. SRJ also at: School of Ocean Sciences, Bangor Univ., Menai Bridge, Anglesey, LL595AB, UK. – J. Kotta, Estonian Marine Inst., Univ. of Tartu, Mäealuse 14, EE-12618 Tallinn, Estonia. – P. Kraufvelin, ARONIA, Coastal Zone Research Team, Åbo Akademi University and Novia University of Applied Sciences, Raseborgsvägen 9, FI-10600 Ekenäs, Finland. – M. Molis and N. Valdivia, Biologische Anstalt Helgoland, Sect. Functional Ecology, Alfred-Wegener-Inst. for Polar and Marine Research, Marine station, Kurpromenade 201, DE-27498 Helgoland, Germany. NV also at: Inst. de Ciencias Marinas y Limnológicas, Facultad de Ciencias, Univ. Austral de Chile, Campus Isla Teja, Valdivia, Chile. – I. Sousa Pinto, Centre of Marine and Environmental Research (CIIMAR), and Dept of Biology, Faculty of Sciences, Univ. of Porto, Rua dos Bragas 289, PT-4050-123 Porto, Portugal.

Compensatory dynamics, overyielding and statistical averaging are mechanisms promoting the temporal stability of natural communities. Using the model of European intertidal rocky shore assemblages and collating 17 datasets, we investigated how the strength of these stability-enhancing mechanisms varies with latitude and how it can be altered by the loss of habitat-formers (e.g. canopy-forming macroalgae). Community stability decreased with increasing latitude, mostly as a consequence of a greater synchronization of species fluctuations. Statistical averaging and overyielding (i.e. richness effect) promoted stability, but their strength did not vary with latitude. An experimental removal of macroalgal canopies caused a strengthening of the statistical averaging effect that was consistent across the latitudinal gradient investigated. Nonetheless, the loss of canopies depressed stability by enhancing the synchronization of species fluctuations on southernmost shores, while it had weak effects on shores at higher latitudes. Variation in life-history traits among canopy-forming species and/

or in prevailing environmental conditions across a gradient of latitude could underlie variable effects of habitat-formers on species fluctuations. Our study shows 1) that the stability of intertidal assemblages and strength of compensatory dynamics varies with latitude, 2) that canopy-forming macroalgae, exerting a strong control on understorey species, can influence the strength of compensatory dynamics and 3) that biological forcing (i.e. facilitation) can be as important as environmental forcing in enhancing the synchronization of species fluctuations.

Concerns over the consequences of biodiversity loss for the ability of ecosystems to supply goods and services to mankind have fuelled research on the diversity-stability hypothesis (Tilman 1996, Chapin et al. 1998, McCann 2000). This has ultimately led to the recognition that com- munity stability can be promoted by different mechanisms (Lehman and Tilman 2000, Cottingham et al. 2001, Loreau and de Mazancourt 2008, Isbell et al. 2009).

Asynchronous species dynamics, fostered by interspecific competition and/or differential response to disturbances

or environmental stress, can sustain stability by generating negative species covariances (Tilman 1999, Yachi and Loreau 1999, Ives et al. 1999, McCann 2000). In addition, when most species perform better in multi- than mono- specific assemblages, temporal stability is enhanced via a greater increase in the average of the aggregate property in respect to its variance. This mechanism, generally referred to as overyielding, occurs whenever the average of a community property increases with species diversity (Lehman and Tilman 2000). Finally, the statistical averaging of fluctuations in the Oikos 000: 001–009, 2012 doi: 10.1111/j.1600-0706.2011.19967.x

© 2011 The Authors. Oikos © 2012 Nordic Society Oikos Subject Editor: Matthew Bracken. Accepted 21 November 2011

(2)

abundances of individual species within a community can lead to greater temporal stability in communities at increas- ing levels of species richness (statistical averaging or portfolio effect; Doak et al. 1998).

The role of these mechanisms and, in particular, of species fluctuations, on stability has been investigated in a variety of terrestrial and aquatic systems, including lacustrine plank- ton, vascular plant communities, invertebrate and vertebrate assemblages (Klug et al. 2000, Fischer et al. 2001, Romanuk and Kolasa 2002, Romanuk et al. 2006, Houlahan et al.

2007, Vasseur and Gaedke 2007, Valone and Barber 2008).

These studies have revealed that a variety of factors, such as species traits and trophic-level, environmental conditions, resource availability and spatial and temporal scale investi- gated, can generate large context-dependency in the strength of the mechanisms underlying community stability.

Little effort has, however, been made to assess how the importance of mechanisms generating stability can vary in space, within a given ecosystem. For instance, there is a trend for increased strength in biological interactions, such as interspecific competition (Connolly et al. 2001, Bertness and Ewanchuk 2002), herbivory (Pennings and Silliman 2005, Coleman et al. 2006) or predation (Vermeij 1978, Sanford et al. 2003), from high to low latitudes. The signifi- cance of asynchronous species fluctuations can, therefore, be expected to vary with latitude, as a consequence of variation in the strength of biological interactions and environmental forcing (Campbell et al. 2011). Predicting the direction of this change is, however, difficult, since the relative impor- tance of weak versus strong interactions (Klug et al. 2000, McCann 2000, Griffin et al. 2009), as well as that of differential response among species to environmental fluc- tuations (Ives et al. 1999, 2000, Yachi and Loreau 1999, Klug et al. 2000), in generating compensatory dynamics is yet to be fully elucidated.

Another aspect that has been poorly explored is the role that habitat-formers or ecosystem engineers (species that create or modify habitats) can play in determining stability levels. The presence of habitat-formers is a major driver of the structure and functioning of species assemblages (Bruno and Bertness 2001). By setting prevailing environmental conditions and, in particular, dampening their oscillations, habitat-formers can modulate the direction and strength of inter-specific interactions (Bruno and Bertness 2001, Kraufvelin et al. 2006, Callaway 2007, Brooker et al. 2008).

Thus, they can be hypothesized to have a large influence on the mechanisms that promote stability. For instance, by modifying species interactions and/or their response to disturbances or environmental stress, habitat-formers could directly govern the synchronization of species fluctuations.

In addition, through their pervasive effects on species iden- tity and relative abundances, they might alter the contribu- tion of statistical averaging and overyielding to stability by modulating evenness (Doak et al. 1998, Cottingham et al.

2001, Li and Stevens 2010; but see Isbell et al. 2009). Alter- ation to species evenness in the presence of habitat-formers, such as canopy-forming macroalgae, seems likely when they are perennial and their abundance/biomass is disproportion- ately greater than that of associated species. Some studies have reported greater stability for dominant than subordi- nate species (Lepš 2004, Steiner et al. 2005, Polley et al.

2007). Thus, as argued by Grman et al. (2010), a large abun- dance of particularly stable species might enhance commu- nity stability by a mechanism similar to the sampling effect (Huston 1997).

We investigated patterns of variation in the stability of intertidal rocky shore assemblages and underlying mecha- nisms along a latitudinal gradient in Europe. Furthermore, we assessed how the mechanisms promoting stability could be altered by the loss of canopy-forming macroalgae. We focused on these habitat-formers since their role in main- taining intertidal biodiversity has been well-documented, and they are reported to be declining on many temperate rocky shores worldwide (North Atlantic: Jenkins et al. 1999;

Mediterranean: Benedetti-Cecchi et al. 2001, Airoldi and Beck 2007; New Zealand: Lilley and Schiel 2006; California:

Thom and Widdowson 1978; Baltic Sea: Vogt and Schramm 1991). Specifically, we tested the hypothesis that the stabil- ity in the cover of sessile rocky intertidal species would vary along a gradient of latitude as a consequence of variation in the synchrony of species fluctuations, statistical averaging and overyielding (i.e. richness effect sensu Cardinale et al.

2006). In addition, we tested the hypothesis that the effect of macroalgal canopy removal on stability and underlying mechanisms would vary between southern and northern European rocky shores. In line with the above mentioned trend for the strength of biological interactions to decrease towards higher latitudes (Vermeij 1978, Connolly et al.

2001, Bertness and Ewanchuk 2002, Sanford et al. 2003, Pennings and Silliman 2005, Coleman et al. 2006), Campbell et al. (2011) have suggested that a weakening of the relation- ship between diversity and stability towards higher latitudes might be generated by the prevalence of physical forcing over biological forcing. In accordance, we predicted that the removal of canopies would have little effect on the stability of rocky intertidal communities at higher latitudes, where physical forcing prevails. In contrast, at lower latitudes, where biological interactions (either negative or positive) play an important role in regulating the relationship between diversity and stability, the removal of canopies should gener- ate a large effect on stability.

Material and methods

Estimates of temporal variance in total cover and in cover of individual taxa are required for analysing temporal stabil- ity of communities and underlying mechanisms. A total of 17 datasets were used to investigate latitudinal patterns in the mechanisms promoting stability (Table 1). Species fluc- tuations can be synchronous at some timescales, but not at others, so that long time-series enabling partitioning at vary- ing scales are of paramount importance to identify discon- tinuities (Vasseur and Gaedke 2007, Downing et al. 2008, Keitt 2008). The overall duration (about two years) and sampling intervals (i.e. 2–6 months) of the studies included in our analyses enable encompassing major environmental fluctuations (i.e. seasonal). Thus, although we cannot pro- vide any insight into longer term trajectories, the data used in this study are adequate to describe short- to mid-term oscillations in rocky benthic assemblages characterized by relatively fast species turn-over.

(3)

Table 1. Details of datasets used in the correlative and experimental analyses, ordered from low to high latitudes. DatasetCountryRegionSampling periodSampling intervalCanopy-forming species/dominant taxaPlot sizeCanopy cover (%)Canopy/understorey 1(1)ItalyIonian Sea (Med.)2006–20073–6 month (5)Cystoseira amentacea var. stricta0.09 m2∼ 932.14 0.28 2(2)PortugalAtlantic2006–20072–5 month (5)Chondrus crispus, Mastocarpus stellatus0.09 m2∼ 431.27 0.44 3ItalyLigurian Sea (Med.)2001–20032–6 month (7)None/EC–AT0.01 m22 4Italy††Ligurian Sea (Med.)2003–20052–6 month (7)None/EC–AT0.06 m22 5(3)ItalyLigurian Sea (Med.)2006–20073–6 month (6)Cystoseira compressa0.09 m2∼ 98 7.6 1.39 6SpainAtlantica2002–20044–6 month (6)Sargassum muticum/EC–AT0.67 m2∼ 122 7(4)FranceNorth Atlantic2006–20084–7 month (4)Ascophyllum nodosum0.25 m2∼ 886.00 1.17 8UKNorth Atlantica2002– 20046–8 month (5)Sargassum muticum/EC–AT0.67 m2∼ 42 9(5)UKNorth Atlantic2006 –20073–6 month (6)Fucus serratus/Fucus vesiculosus0.09 cm2∼ 690.34 0.22 10(6)IrelandNorth Atlantic2006– 20073–6 month (7)Fucus serratus/Fucus vesiculosus0.09 m2∼ 801.61 0.30 11(7)GermanyNorth Sea2006 20073–6 month (7)Fucus serratus0.09 m2∼ 840.78 0.02 12(8)GermanyNorth Sea2004 20073–6 month (7)Fucus serratus0.09 m2∼ 950.79 0.07 13(9)UKNorth Atlantic2006 –20083–6 month (6)Fucus serratus0.09 m2∼ 890.68 0.04 Experimental datasets used to assess the effects of canopy removal on stability and underlying mechanisms are reported in brackets under the Dataset column; this numbering order is followed in Fig. 2; the total number of sampling events is reported in brackets in the Sampling interval column. athese datasets had a spatial structure (replicated sites) and generated 3 subsets of data. Dominant taxa are reported for the cases in which canopy-formers were absent (dataset 3, 4) or not dominant (dataset 6, 8). Canopy cover (%) refers to the time at which the experiment was shortly started. The ratio between the cover of the canopy versus that of the understorey sessile assemblage ( 1 SE) is reported under the column Canopy/understorey. Bertocci et al. 2010, Mar. Ecol. Prog. Ser. 414: 107–116; Bertocci et al. 2010, Ecology 86: 2061–2067; ††Vaselli et al. 2008, Mar. Ecol. Prog. Ser. 364: 57–66. EC Encrusting corallines; AT Algal turfs.

A subset of nine datasets including the experimental removal of canopy-forming macroalgae were further used to test our hypothesis on the effects of the loss of this mor- phological group on stability and underlying mechanisms (Table 1). Canopy-forming species varied among sites (Table 1). Except for Site 4, where canopies were made of Ascophyllum nodosum, Fucus serratus and F. vesiculosus were the main canopy-formers on northern shores. In contrast, species forming canopies were more variable at lower lati- tudes: Chondrus crispus and Mastocarpus stellatus on the coast of Portugal, Cystoseira compressa in the Ligurian Sea and Cystoseira amentacea var. stricta in the Ionian Sea.

In all cases, canopies were removed at the beginning of the experiment, recruits were selectively removed there- after with no further disturbance to other species and sampling started about three months after the initial treat- ment. Canopy-forming species were removed by hand to minimize disturbance to understorey assemblages. At the beginning of the experiment, the cover of the canopy var- ied among sites (Table 1), but there was not a latitudinal pattern (Spearman rs  0.05, p  0.90). In contrast, the ratio between the cover of the canopy and that of under- storey assemblages showed a marked trend to decrease when moving from southern to northern shores (Table 1), although this correlation was not significant (Spearman rs  20.62, p  0.07).

The percentage cover of all macroscopic sessile taxa ( 1 mm) was quantified visually in each study by means of grids divided into sub-quadrats, except for datasets 6 and 8 where it was estimated with the point-intercept method.

Across datasets, the size of plots varied between 0.01 and 0.67 m2 (Table 1), but it was not correlated with latitude (Spearman rs  20.05, p  0.86). Thus, although larger plots were more effective in sampling rare species (signifi- cant positive correlation between plot size and number of singletons: Spearman rs  0.79, p  0.0001) that are likely to exhibit large temporal variability in cover, latitudinal pat- terns in stability and underlying mechanisms were indepen- dent of plot size.

In marine environments, where competition for primary space among sessile organisms is generally strong, cover is an important property of communities (Connolly and Muko 2003). In addition, since rocky benthic assemblages can be multi-layered, the total percentage cover of organisms is not constrained to 100% and can be reasonably taken as a proxy for biomass (Cavanaugh et al. 2010).

For each plot, temporal stability of cover at the com- munity level was estimated as the ratio between the mean (across the time series) and the standard deviation of per- centage cover (m/s, the inverse of the coefficient of variation;

Lehman and Tilman 2000). Since variations in temporal sta- bility can be generated by changes in either the numerator, the denominator or both, we formally analysed variations in m and s, across a latitudinal gradient and following the experimental removal of algal canopies.

The degree of synchrony of species fluctuations has often been examined by calculating the sum of all pair-wise species covariances in a plot and interpreting negative plot covariances as evidence of the prevalence of asynchronous fluctuations and, hence, of a positive contribution of the cova- riance effect to community stability (Lehman and Tilman

(4)

among them. Assumptions of linearity and homogeneity of variances were checked by visual inspection of residual plots.

Log transformation was effective in removing non-linearity and variance heterogeneity in response variables. BCa (bias-corrected accelerated percentile) bootstrap confidence intervals set at 95% were calculated using 999 iterations.

Unfortunately, the geographical positioning of sites for which experimental data were available (Table 1) did not allow assessment of variation in the effects of the removal of macroalgal canopies along a latitudinal gradient using a regression approach. Thus, data were analyzed by means of a two-way factorial ANOVA, including the factors Site (random) and Canopy (fixed, control versus removal). The shores investigated were subsequently separated into north- ern and southern according to prevalent climatic conditions.

In particular, shores investigated along the coasts of Italy and Portugal ( 45°N of latitude) are characterized by a Mediterranean climate (Lusitanian-Mediterranean biore- gion, with hot, dry summers and warm, wet winters), while those investigated at higher latitudes ( 45°N of latitude), except for those in the North Sea experiencing cold winters, are under the influence of an oceanic climate (Eastern Atlan- tic Boreal bioregion, with mild winters and cool summers).

Evidence of variation in the effects of the canopy removal with latitude was, however, not conclusive. Data for 8 out of the 9 sites analyzed had 5 replicates (n  5) for each of the con- trol and the canopy removal treatment. In order to maintain a balanced design and enable a straightforward analysis, the same number of plots was randomly selected from the greater number available for both control and canopy-removal plots at the remainder site (i.e. n  8 experimental dataset 4, in Table 1). Homogeneity of variances was checked by means of Cochran’s test (Underwood 1997). In some cases, it could not be achieved by transformation, but data were analyzed nonetheless, since analysis of variance is robust to departure from this assumption when there are many independent replicates and sizes of samples are equal (Underwood 1997).

Results were, however, interpreted with caution, by judging significance more conservatively (a  0.01). SNK tests were used for a posteriori comparisons of the means.

Results

The stability of rocky shore assemblages decreased signifi- cantly from southern to northern shores (y  1.339 2 0.013x;

F1,94  8.31, p  0.01, RAdj2  0.07, CI  20.023, 20.005;

Fig. 1A). Both total assemblage cover (y  1.655  0.008x;

F1,94  10.22, p  0.01, RAdj2  0.09, CI  20.008, 0.017) and standard deviation (y  0.348  0.021x; F1,94  17.25, p  0.001, RAdj2  0.15, CI  0.004, 0.030) significantly increased with latitude.

Species synchrony also increased with latitude (y  22.608  0.034 x; F1,94  24.24, p  0.001, RAdj2  0.20, CI  0.005, 0.049; Fig. 1B), indicating a weakening of the covariance effect when moving from southern to north- ern rocky shores. In contrast, there was no significant rela- tionship between latitude and richness effect (F1,94  3.25, p  0.05), mean-variance scaling coefficient z (F1,94  1.94, p  0.05) or evenness (F1,94  0.01, p  0.05). Importantly, z, ranging between 1.19 and 1.79 across sites, was always 2000, Cottingham et al. 2001). The validity of this metric

has been recently challenged by Loreau and de Mazancourt (2008), who have argued that it does not allow comparisons between communities differing in species richness and that the underlying assumption of species fluctuating indepen- dently is highly unrealistic. Here, community-wide synchrony in species cover (ϕc) was calculated for each plot by means of a measure of synchrony recently proposed by the same authors (Loreau and de Mazancourt 2008). This is calculated as ϕc σcT ci

i

s

2

1 2

∑

 

 , where scT2 is the variance in total community cover and sci is the standard deviation in cover of species i, in a community with S species. This statistic varies between 0 (perfect asynchrony) and 1 (perfect syn- chrony) and makes no specific assumption about the magni- tude and distribution of species abundances and variances.

The strength of the statistical averaging effect is depen- dent upon the scaling relationship between the mean and the variance (mean-variance rescaling, Tilman 1999). This relationship follows Taylor’s power law: S2  cmz, where S2 is the variance, c is a constant, m is the mean and z is the scaling coefficient. Larger values of z indicate a more rapid increment in the variance with the mean and, assuming that species in a community are independent, have equal abun- dances and mean-variance rescaling coefficients, statistical averaging is supposed to promote stability whenever z  1.

Thus, z was calculated for each taxon in each plot as the slope of the regression of log(variance) versus log(mean).

In order to assess how variations in the value of z could be related to variations in species dominance (Doak et al.

1998, Cottingham et al. 2001), we assumed an exponential rank–abundance distribution; taxa were ranked in decreasing order of abundance, so that the contribution of the ith taxon becomes mi  m1e2a(i21), where m1 is the most abundant taxon and a is the coefficient determining the rate at which mean abundance decreases with increasing rank (Doak et al.

1998). Thus, larger values of a indicate greater inequality in abundance (i.e. lower evenness).

In general, if a species mixture performs better than com- ponent monocultures there is overyielding. However, as noted by Fridley (2001), it is possible to distinguish between the case in which a diverse assemblage performs more effec- tively than the average of the component monocultures (i.e.

richness effect sensu Cardinale et al. 2006) and that in which a diverse assemblage performs more effectively then the best performing component monoculture (i.e. complementarity effect sensu Cardinale et al. 2006). Here, overyielding was estimated as the slope of the regression of total community cover versus taxa richness in each plot (Tilman 1999, Lehman and Tilman 2000). Thus, following Cardinale et al. (2006), it will hereafter be referred to as a richness effect. The differ- ent times of sampling were used as replicates and slopes were calculated by means of a linear mixed effect model (Crawley 2002), in order to take into account the autocorrelation in residuals (i.e. plots repeatedly sampled through time).

In order to correct for differences in the sampling effort among descriptive datasets (the number of replicates vary- ing between 5 and 8), weighted regression was used to investigate the relationship between response variables and latitude. Weights were calculated as the ratio between the number of replicates available for each study and the variance

(5)

(A)

(B)

(C)

Latitude

40 45 50 55

Temporal stability in cover (µ/σ)

0.0 0.2 0.4 0.6 0.8 1.0 1.2 1.4

Latitude

40 45 50 55

Species synchrony (ϕ)

–2.5 –2.0 –1.5 –1.0 –0.5 0.0

Species synchrony (ϕ)

–1.0 –0.5 0.0 0.5 1.0

Temporal stability in cover (µ/σ)

0.0 0.2 0.4 0.6 0.8 1.0 1.2 1.4

Figure 1. Regressions of (A) temporal stability in cover (m/s) and (B) species synchrony (ϕ) against latitude. Estimates of temporal stability and species synchrony have been log transformed before the analysis to improve linearity and remove heterogeneity of vari- ances. The relationship between stability and species synchrony (C) is also reported to illustrate the importance of this mechanism in determining variations in stability along a latitudinal gradient. The use of residuals from the regression of species synchrony against latitude guarantees that the relationship between stability and spe- cies synchrony was not generated by the correlation of both vari- ables with latitude.

greater than 1, suggesting that the statistical averaging effect was ubiquitous along the latitudinal range investigated. The large decrease in temporal stability (m/s) with increasing syn- chronization (ϕc) of species fluctuations (y  0.697 2 0.317x;

F1,94  41.07, p  0.001, RAdj2  0.30, CI  20.402, 20.209;

Fig 1C) suggests that this mechanism was the main driver of the reduction in stability towards higher latitudes.

In general, the effects of the experimental removal of canopy-forming macroalgae on stability and underlying mechanisms varied among sites (Table 2). Removing the canopy resulted in a significant decrease in temporal stabil- ity only at the four southernmost sites (Table 2, Fig. 2A).

Except for one site, it also caused a decline in mean total cover (Table 2, Fig. 2B). Worth noting is that the magnitude of this effect was particularly large at some of the northern sites (Fig. 2B). In contrast, the standard deviation of cover was significantly altered by the removal of the canopy only at a few sites (Table 2); however, it tended to increase with canopy loss at southern sites and decrease at northern sites (Fig. 2C). Like standard deviation, significant effects of the treatment on the synchronization of species fluctua- tions emerged throughout the latitudinal range investigated (Table 2, Fig. 2D). However, species fluctuations tended to become more synchronous at southern sites when algal canopies were removed, while an opposite trend emerged for sites at higher latitudes (Fig. 2D).

The removal of the canopy caused an increase in the mean-variance scaling coefficient, z, suggesting a general- ized enhancement of the statistical averaging; this effect was, however, significant at some sites, but not at others (Table 2, Fig. 2E). Likewise, removing canopies fostered evenness, but only at some sites (Table 2, Fig. 2F). Finally, the richness effect did not vary between control and canopy removal plots (Table 2).

Discussion

The temporal stability (m/s) in the cover of rocky ben- thic communities tended to decrease with increasing lati- tude. This pattern can result from a decrease in the mean or an increase in the standard deviation of the aggregate property or both (Lehman and Tilman 2000). Both mean total cover (m), and the standard deviation of cover (s), increased with latitude, but the negative relationship between stability (m/s) and latitude suggests that the pro- portional increment in total assemblage cover was smaller than that of standard deviations. Statistical averaging contributed to enhance stability (i.e. z  1), but effects were invariant across the latitudinal gradient. Although the relationship between cover and species richness (i.e.

richness effect) was positive (overyielding) in some plots (∼ 78%) and negative (underyielding) in others (∼ 22%), no general pattern emerged across the latitudinal range investigated. Therefore, the reduction in stability towards higher latitudes was mainly driven by greater synchroniza- tion of species fluctuations, ultimately resulting in positive or less negative summed species covariances (Lehman and Tilman 2000). These patterns indicate that compensatory dynamics (i.e. the covariance effect) are neither ubiqui- tous nor rare, but they are likely to vary in space, being influenced by a complex mix of biological and physical processes (Valdivia and Molis 2009).

The prevalence of positive or less negative species cova- riances (i.e. synchronous species fluctuations) has often been explained by inferring a greater signature of environ- mental forcing relative to that of biological processes, such as competition or predation (Houlahan et al. 2007, Valone

(6)

Table 2. ANOVA of the effects of Treatment (canopy present vs canopy removal) and Site on temporal stability (m/s), mean cover (m), standard deviation (s), species fluctuations (ϕ), statistical averaging (z), richness effect and evenness (a). Degrees of freedom for each term and interac- tion included in the analysis are reported in brackets. **p  0.01; ***p  0.001.

Treatment  Tr (1) Site  Si (8) Tr  Si (8) Residual (72) Cochran’s test

Source of variation MS F MS F MS F MS Transformation

Response variable

Temporal stability (m/s) 130.265 5.03 30.37 4.95*** 25.922 4.22*** 6.136 none p  0.01 Mean (m) 57470.630 24.73** 9964.892 35.48*** 2324.129 8.28*** 280.833 none p  0.05

Std dev. (s) 567.449 0.73 1051.194 9.20*** 775.277 6.79*** 114.261 none p  0.01

Species synchrony (ϕ) 0.176 3.07 0.083 10.21*** 0.058 7.05*** 0.008 none p  0.05

Statistical averaging (z) 1.115 20.67** 0.291 13.25*** 0.054 2.46* 0.022 none p  0.01

Richness effect 0.001 0.09 0.067 18.20*** 0.007 1.84 0.004 none p  0.01

Evenness (a) 0.450 1.95 0.355 13.76*** 0.231 8.97*** 0.026 ln(x  1) p  0.05

and Barber 2008). A recent meta-analysis, including both aquatic and terrestrial environments, has reported a weaken- ing of the stabilizing effect of richness as latitude increased (Campbell et al. 2011). Speculating on this pattern, the same

authors (Campbell et al. 2011) have inferred that, at high latitudes, environmental forcing would prevail on biological drivers (i.e. negative species interactions, such as competition and predation) in shaping the relationship between diversity

(B)

(C) (D)

Temporal stability in cover (µ/σ) 0 4 8 12

16 Control

Removal

* *

*

*

(A)

*

*

*

*

* * *

*

Mean total cover (%)

0 50 100 150 200 250

(E)

* *

*

Standard deviation in cover ) *

0 20 40 60 80 100

Statistical averaging (z)

0.0 0.5 1.0 1.5 2.0 2.5

* *

(F)

Evenness (a)

0.0 0.5 1.0 1.5

*

*

*

Site

Species synchrony (ϕ)

0.0 0.2 0.4 0.6 0.8 1.0

*

*

* *

*

*

* * *

1 2 3 4 5 6 7 8 9

Northern Europe Southern Europe

1 2 3 4 5 6 7 8 9

Northern Europe Southern Europe

Figure 2. Effects of canopy removal at different European sites on (A) stability in community cover (m/s), (B) mean community cover (m), (C) standard deviation in community cover (s), (D) species synchrony (ϕ), (E) mean-variance scaling coefficient (z) and (F) evenness (a).

Sites on the x-axis are ordered following an increasing latitudinal gradient according to the numbering presented in Table 1 and divided in the groups Southern Europe (below 45°N) and Northern Europe (above 45°N). Data are means  SE (n  5). Asterisks indicate significant differences between the control and the canopy removal treatment for each site.

(7)

understorey assemblages (Table 1). This suggests that under- storey species compensated (i.e. increased in cover) for the decline in mean community cover caused by the elimination of the canopy-forming species. A trend for species fluctua- tions to become more synchronous following the removal of the canopy would confirm that most species responded posi- tively to changed environmental conditions. Thus, at Sites 2 and 3, the enhanced strength of the statistical averaging effect caused by the removal of the canopy was not sufficient to counter destabilizing effects of smaller community cover and more positive species covariances.

At northern sites (except for Site 4), the large decrease in mean community cover (m), mainly generated by the loss of the canopy-forming species, was compensated for by a decrease in the standard deviation of community cover (s).

This ultimately resulted in little overall change in temporal stability (m/s). Similar compensation between destabiliz- ing effects arising from decreased abundance and stabiliz- ing effects, due to decreased temporal variability, have been recently documented in a subtidal marine system (Long et al. 2011).

Which mechanisms sustained community stability at northern sites, in the face of destabilizing effects of decreased mean cover? The removal of the canopy, generating less synchronous species fluctuations, promoted the stabilizing effects of compensatory dynamics. This, along with a gener- alized strengthening of statistical averaging, was effective in countering destabilizing effects due to the decline in com- munity cover (Fig. 2). Thus, although the loss of dominant canopy-forming species led to a decline of community cover, the strengthening of the mechanisms promoting stability in response to disturbance was able to provide an insurance against the collapse of this ecosystem function. This sug- gests that a large abundance of particularly stable species (i.e.

canopy-forming species on rocky shores) does not always enhance overall community stability (Lepš 2004, Polley et al.

2007, Grman et al. 2010).

The occurrence of different canopy-forming species across the European shores investigated prevents assess- ing to what extent the impact of their loss on stability and underlying mechanisms was driven by local environmental conditions or by species-specific life traits. On southern shores, manipulated canopy-forming species varied from Chondrus crispus and Mastocarpus stellatus on Atlantic coasts of Portugal (Site 2), to smaller sized Cystoseira compressa and C. amentacea var. strycta on shores located in SE (Site 1) and NW (Site 3) Italy, respectively. Although these species largely differ in both architecture and size, their removal caused a consistent increase in the synchron- ization of species fluctuations and a drop in stability on southern shores. In contrast, on northern shores, the effects of removing Fucus spp. were markedly different from those of removing the canopies formed by Ascophyllum nodosum (at Site 4) that were more similar to those recorded at southern sites.

The ratio between canopy and understorey assemblage covers might have played an important role in determin- ing the response of species fluctuations and stability to the removal of canopies formed by different species. This ratio was generally small at sites were canopies where made by and stability. The same mechanism could be invoked as an

explanation for the greater synchrony of species fluctuations on rocky shores at higher latitudes, where fluctuations in physical variables (e.g. light, temperature) are wider than on shores at lower latitudes.

Stress due to desiccation and heat is an important deter- minant of the structure and dynamics of rocky intertidal assemblages (Connell 1972). As shown by Helmuth et al.

(2002), thermal stress is regulated by the interplay between tidal amplitude and timing of low tides and, hence, it does not decrease linearly with increasing latitude. Indeed, on the west coast of the United States, some northern sites were more thermally stressful than some southern sites for intertidal invertebrates, suggesting that the interaction between climate and timing of low tides can create a com- plex mosaic of thermal environments along a gradient of latitude (Helmuth et al. 2002). Detailed information on tidal regimes, comparable to that produced by Helmuth et al. (2002) for the west coast of the United States, is, to the best of our knowledge, not available for the European coasts investigated. Nonetheless, if we assume the occur- rence of a mosaic of thermal environments (Helmuth et al.

2002), the linearity in the variation of stability and species synchrony with latitude would suggest a greater influence of other environmental variables covarying with latitude (i.e. light, temperature) than that of tidal amplitude and timing of low tides. This does not, by any means, imply that the interaction between the tidal regime and local climate plays no role in generating latitudinal patterns in stability and species synchrony at the sites we investigated.

Alternatively, variation in temporal dynamics of popula- tions might underlie the latitudinal pattern in species syn- chrony. The temporal turn-over of species composition slows down towards higher latitudes, as a consequence of lower mean temperatures (Shurin et al. 2007). The temporal scale necessary to observe strong diversity effects on stability might be longer at high latitudes, due to slower population dynam- ics of species (Campbell et al. 2011). Thus, when investi- gated over a two-year temporal scale, the stabilizing effect of compensatory dynamics could have emerged on shores at lower latitudes, where species turn-over is faster, but not on those at higher latitudes, where species turn-over is slower.

The removal of canopy-forming macroalgae had a strong negative impact on temporal stability only at four sites;

interestingly, these were the southernmost investigated.

Removing algal canopies caused a generalized decrease in mean covers, but this was smaller at the four most southern sites (ranging between 20.0 and 30.0%; mean  SE: 21  3.8) than at the five most northern sites (ranging between 40.0 and 97.0%; mean  SE: 71.85  10.6). The standard devia- tion of cover was significantly altered by the removal of the canopy only at a few sites, but it tended to increase with canopy loss at southern sites and decrease at northern sites (Fig. 2C).

Thus, at southern sites, changes in both m (decreasing) and s (increasing) of cover after canopy removal were desta- bilizing in direction and caused a decline in temporal sta- bility. At these sites, the drop in mean community cover caused by the canopy removal was not as large as it could be expected from the large ratio of canopy cover to that of

(8)

results suggest that the potential of biological interactions to generate positive covariances (i.e. biological forcing) has been greatly overlooked (but see Wilby and Shachak 2004, Steiner et al. 2005). In some cases, habitat-formers would be able to synchronize species fluctuations over the levels generated by local physical conditions. Thus, greater synchronization of species fluctuations does not necessarily reflect a prevalence of environmental forcing over biological forcing, as often assumed (Houlahan et al. 2007, Valone and Barber 2008, Campbell et al. 2011). For these reasons, framing the biodiversity–stability relationship into facilitation theories, such as the stress-gradient hypothesis (Bertness and Callaway 1994), might contribute to reconcile contrasting effects of biodiversity reported in the literature (Cottingham et al. 2001) by enabling a more balanced account of abiotic and biotic forces at play.

Acknowledgements – We sincerely thank D. Vasseur and P. Petraitis for providing valuable comments on an earlier version of the ms.

The final version has been greatly improved by insightful comments and constructive criticism from M. Bracken. The project has been carried out in the framework of the MarBEF Network of Excellence

‘Marine Biodiversity and Ecosystem Functioning’ which was funded by the Sustainable Development, Global Change and Ecosystems Programme of the European Community’s Sixth Framework Programme (contract no. GOCE-CT-2003-505446).

While writing, FB was supported from an Assegno di Ricerca from the University of Sassari.

References

Airoldi, L. and Beck, M. W. 2007. Loss, status and trends for coastal marine habitats of Europe. – Oceanogr. Mar. Biol.

Annu. Rev. 45: 345–405.

Benedetti-Cecchi, L. et al. 2001. Predicting the consequences of anthropogenic disturbance: large-scale effects of loss of canopy algae on rocky shores. – Mar. Ecol. Prog. Ser. 214: 137–150.

Bertness, M. D. and Callaway, R. 1994. Positive interactions in communities. – Trends Ecol. Evol. 9: 191–193.

Bertness, M. D. and Ewanchuk, P. J. 2002. Latitudinal and climate-driven variation in the strength and nature of biologi- cal interactions in New England salt marshes. – Oecologia 132: 392–401.

Brooker, R. W. et al. 2008. Facilitation in plant communities:

the past, the present and the future. – J. Ecol. 96: 18–34.

Bruno, J. F. and Bertness, M. D. 2001. Habitat modification and facilitation in benthic marine communities. – In: Bertness M. D. et al. (eds), Marine community ecology. Sinauer, pp. 201–218.

Bulleri, F. 2009. Facilitation research in marine systems: state of the art, emerging patterns and insights for future developments.

– J. Ecol. 97: 1121–1130.

Callaway, R. M. 2007. Positive interactions and interdependence in plant communities. – Springer.

Campbell, V. et al. 2011. Experimental design and the outcome and interpretation of diversity-stability relations. – Oikos 120:

399–408.

Cardinale, B. J. et al. 2006. Effects of biodiversity on the functioning of trophic groups and ecosystems. – Nature 443: 989–992.

Cavanaugh, K. C. et al. 2010. Scaling giant kelp field measure- ments to regional scales using satellite observations. – Mar.

Ecol. Prog. Ser. 403: 13–27.

Chapin, F. S. et al. 1998. Ecosystem consequences of changing biodiversity - experimental evidence and a research agenda for the future. – Bioscience 48: 45–52.

Fucoids, while it was larger in the presence of other canopy- forming species (i.e. at Sites 1 to 4). This suggests that species-specific traits of habitat-formers could generate variation in their effects on the synchronization of species fluctuation and stability of associated assemblages. More specifically, attributes of Fucoids, such as size, architecture and toughness of tissues, might modify environmental conditions in such a way to enhance the synchronization of species fluctuations.

On the other hand, effects of canopy-forming macro- algae on understorey organisms have been previously shown to vary with latitude (Leonard 2000). For instance, on the east coast of the USA, the effects of canopies formed by Ascophyllum nodosum on associated organisms (i.e. barna- cles) were positive at southern sites, but negative at northern ones (Leonard 2000). In addition, even slight variations in climate (i.e. maximum daily temperatures) were sufficient to alter the sign of the interactions between the habitat- former and the associated species (Leonard 2000). More generally, the occurrence of positive species interactions is predicted to increase along an increasing gradient of stress (i.e. the stress-gradient hypothesis; Bertness and Callaway 1994). While predictions from this conceptual framework have been tested and refined in a variety of environments (Callaway 2007, Brooker et al. 2008, Bulleri 2009), the implications of shifts in the sign and strength of species interactions on stability and underlying mechanisms remain largely unexplored.

By dampening variations in physical conditions, the presence of macroalgal canopies would be predicted to reduce the signature of environmental forcing, resulting in the prevalence of biological interactions, such as com- petition and, hence, of less synchronous species fluctua- tions (Houlahan et al. 2007, Valone and Barber 2008). On shores at higher latitudes, species fluctuations showed, in contrast, a consistent tendency to become less synchronous following the experimental removal of the canopy-forming Fucus spp. This means that most species started fluctuating more asynchronously when fully exposed to variations in physical variables (e.g. light and temperature) that are par- ticularly wide at high latitudes. Thus, on northern shores, the effects of biological forcing (i.e. the presence of canopy- forming macroalgae) in synchronising species fluctuations overwhelmed those of environmental forcing.

At the four most southern European sites, synchrony in species fluctuations tended to increase in canopy removal plots. Amelioration of harsh physical conditions (i.e. desic- cation and heat) by the canopy could have enhanced negative species interactions among understorey species, in line with predictions from the stress-gradient hypothesis (Bertness and Callaway 1994). Once deprived of a canopy, most of the species could have tracked more closely variations in environmental conditions, resulting in a greater synchron- ization of their fluctuations (Houlahan et al. 2007, Valone and Barber 2008, Engelen and Santos 2009).

Our findings, together with those of Campbell et al.

(2011), point towards the occurrence of a latitudinal trend in the stability of natural communities. This would be mostly produced by variations in the contribution of compensatory dynamics, at odds with the more consistent contribution of statistical averaging and richness effect. In addition, our

(9)

Lepš, J. 2004. Variability in population and community biomass in a grassland community affected by environmental produc- tivity and diversity. – Oikos 107: 64–71.

Li, W. and Stevens, M. H. H. 2010. How enrichment, ecosystem size, and their effects on species richness co-determine the sta- bility of microcosm communities. – Oikos 119: 686–695.

Lilley, S. A. and Schiel, D. R. 2006. Community effects following the deletion of a habitat-forming alga from rocky marine shores. – Oecologia 148: 672–681.

Long, Z. T. et al. 2011. Food chain length and omnivory determine the stability of a marine subtidal food web. – J. Anim. Ecol.

80: 586–594.

Loreau, M. and de Mazancourt, C. 2008. Species synchrony and its drivers: neutral and nonneutral community dynamics in fluctuating environments. – Am. Nat. 172: 48–66.

McCann, K. S. 2000. The diversity–stability debate. – Nature 405:

228–233.

Pennings, S. C. and Silliman, B. R. 2005. Linking biogeography and community ecology: latitudinal variation in plant–herbivore interaction strength. – Ecology 86: 2310–2319.

Polley, H. W. et al. 2007. Dominant species constrain effects of species diversity on temporal variability in biomass production of tallgrass prairie. – Oikos 116: 2044–2052.

Romanuk, T. N. and Kolasa, J. 2002. Environmental variability alters the relationship between richness and variability of community abundances in aquatic rock pool microcosms.

– Ecoscience 9: 55–62.

Romanuk, T. N. et al. 2006. Nutrient enrichment weakens the stabilizing effect of species richness. – Oikos 114: 291–302 Sanford, E. et al. 2003. Local selection and latitudinal variation

in a marine predator–prey interaction. – Science 300:

1135–1137.

Shurin, J. B. et al. 2007. Diversity–stability relationship varies with latitude in zooplankton. – Ecol. Lett. 10: 127–134.

Steiner, C. F. et al. 2005. The influence of consumer diversity and indirect facilitation on trophic level biomass and stability.

– Oikos 110: 556–566.

Thom, R. M. and Widdowson, T. B. 1978. A resurvey of E.

Yale Dawson’s 42 intertidal algal transects on the southern California mainland after 15 years. – Bull. S. Calif. Acad. Sci.

77: 1–13.

Tilman, D. 1996. Biodiversity: population versus ecosystem stability. – Ecology 77: 350–363.

Tilman, D. 1999. The ecological consequences of changes in biodiversity: a search for general principles. – Ecology 80:

1455–1474.

Underwood, A. J. 1997. Experiments in ecology. – Cambridge Univ. Press.

Valdivia, N. and Molis, M. 2009. Observational evidence of a negative biodiversity-stability relationship in intertidal epibenthic communities. – Aquat. Biol. 4: 263–271.

Valone, T. J. and Barber, N. A. 2008. An empirical evaluation of the insurance hypothesis in diversity–stability models.

– Ecology 89: 522–531.

Vasseur, D. A. and Gaedke, U. 2007. Spectral analysis unmasks synchronous and compensatory dynamics in plankton com- munities. – Ecology 88: 2058–2071.

Vermeij, G. J. 1978. Biogeography and adaptation. – Harvard Univ. Press.

Vogt, H. and Schramm, W. 1991. Conspicuous decline of Fucus in Kiel Bay (western Baltic): what are the causes? – Mar. Ecol.

Prog. Ser. 69: 189–194.

Wilby, A. and Shachak, M. 2004. Shrubs, granivores and annual plant community stability in an arid ecosystem. – Oikos 106:

209–216.

Yachi, S. and Loreau, M. 1999. Biodiversity and ecosystem productivity in a fluctuating environment: the insurance hypothesis. – Proc. Natl Acad. Sci. USA 96: 1463–1468.

Coleman, R. A. et al. 2006. A continental scale evaluation of the role of limpet grazing on rocky shores. – Oecologia 147:

556–564.

Connell, J. H. 1972. The ecology of rocky shores. – Annu. Rev.

Ecol. Syst. 3: 169–192.

Connolly, S. R. and Muko, S. 2003. Space preemption, size- dependent competition, and the coexistence of clonal growth forms. – Ecology 84: 2979–2988.

Connolly, S. R. et al. 2001. A latitudinal gradient in recruitment of invertebrates in the northeast Pacific Ocean. – Ecology 82:

1789–1813.

Cottingham, K. L. et al. 2001. Biodiversity may regulate the tem- poral variability of ecological systems. – Ecol. Lett. 4: 72–85.

Crawley, M. J. 2002. Statistical computing: an introduction to data analysis using S-Plus. – Wiley.

Doak, D. F. et al. 1998. The statistical inevitability of stability–

diversity relationships in community ecology. – Am. Nat. 151:

264–276.

Downing, A. L. et al. 2008. Environmental fluctuations induce scale-dependent compensation and increase stability in plank- ton ecosystems. – Ecology 89: 3204–3214.

Engelen, A. and Santos, R. 2009. Which demographic traits determine population growth in the invasive brown seaweed Sargassum muticum? – J. Ecol. 97: 675–684.

Fischer, J. M. et al. 2001. Compensatory dynamics in zooplankton community responses to acidification: measurement and mechanisms. – Ecol Appl. 11: 1060–1072.

Fridley, J. D. 2001. The influence of species diversity on ecosystem productivity: how, where and why? – Oikos 93: 514–526.

Griffin, J. N. et al. 2009. Biodiversity and the stability of ecosystem functioning. – In: S. Naeem, D. E. et al. (eds), Biodiversity, ecosystem functioning, and human wellbeing: an ecological and economic perspective. Oxford Univ. Press, pp. 78–93.

Grman, E. et al. 2010. Mechanisms contributing to stability in ecosystem function depend on the environmental context.

– Ecol Lett. 13: 1400–1410.

Helmuth, B. et al. 2002. Climate change and latitudinal patterns of intertidal thermal stress. – Science 298: 1015–1017.

Houlahan, J. E. et al. 2007. Compensatory dynamics are rare in natural ecological communities. – Proc. Natl Acad. Sci. USA 104: 3273–3277.

Huston, M. A. 1997. Hidden treatments in ecological experi- ments: re-evaluating the ecosystem function of biodiversity.

– Oecologia 110: 449–460.

Isbell, F. I. et al. 2009. Biodiversity, productivity and the temporal stability of productivity: patterns and processes. – Ecol. Lett.

12: 443–451.

Ives, A. R. et al. 1999. Stability and variability in competitive communities. – Science 286: 542–544.

Ives, A. R. et al. 2000. Stability and species richness in complex communities. – Ecol. Lett. 3: 399–411.

Jenkins, S. R. et al. 1999. Direct and indirect effects of a macroalgal canopy and limpet grazing in structuring a sheltered inter-tidal community. – Mar. Ecol. Prog. Ser. 188: 81–92.

Keitt, T. H. 2008. Coherent ecological dynamics induced by large-scale disturbance. – Nature 454: 331–334.

Klug, J. L. et al. 2000. Compensatory dynamics in planktonic community responses to pH perturbations. – Ecology 81:

387–398.

Kraufvelin, P. et al. 2006. Nutrient addition to experimental rocky shore communities revisited: delayed responses, rapid recovery.

– Ecosystems 7: 1076–1093.

Lehman, C. L. and Tilman, D. 2000. Biodiversity, stability and productivity in competitive communities. – Am. Nat. 156:

534–552.

Leonard, G. H. 2000. Latitudinal variation in species interactions:

a test in the New England rocky intertidal zone. – Ecology 81:

1015–1030.

Figure

Updating...

References

Related subjects :