Distribution patterns of the peracarid crustaceans associated with the alga Corallina elongata along the intertidal rocky shores of the Iberian Peninsula
© Springer-Verlag and AWI 2010
Received: 9 February 2010
Accepted: 14 July 2010
Published: 28 July 2010
Spatial patterns of intertidal peracarids, associated with the alga Corallina elongata, were studied along the whole Iberian Peninsula. A total of 28,215 specimens were collected, comprising 78 different species (57 amphipods, 16 isopods, 4 tanaids and 1 cumacean), most of them with Atlantic-Mediterranean distribution (60%) and only 9% of Mediterranean endemics. Gammarids were dominant in abundance and number of species, representing more than 70% of the total peracarids. The most common species collected during the present study were the caprellid Caprella penantis, the gammarids Hyale schmidti, Hyale stebbingi, Jassa cf. falcata and Stenothoe monoculoides, the isopod Ischyromene lacazei and the tanaid Tanais dulongii. Caprellids and tanaidaceans presented their highest populations in the stations of the Strait of Gibraltar, whereas isopods were more abundant in Atlantic stations. Univariate analyses did not reflected differences in number of species, abundance and Shannon-Weaver diversity between Mediterranean and Atlantic. However, cluster analyses and Whittaker index, as measure of ß-diversity, showed a different species composition between Mediterranean and Atlantic and a replacement of species along the coast, especially at the Strait of Gibraltar. The turnover mainly affected species of the same genera, probably related with sympatric speciation. CCA and BIO-ENV analyses showed high correlations between environmental measures (especially conductivity) and peracarid distribution. Mediterranean species tolerated higher values of conductivity and temperature, while Atlantic species were associated with stations characterized by higher oxygen concentrations.
Understanding assemblages of organisms is based on the quantitative description of patterns of distribution and abundance of species (Andrew and Mapstone 1987; Underwood et al. 2000), which has become one of the main challenges that studies on biogeography have to face nowadays (Pereira et al. 2006). The borders in an ecological level are often attributed to climatic conditions (Repasky 1991; Wardell-Johnson and Roberts 1993) or antagonistic relationships of competition and predation (Hersteinsson and McDonald 1992). Likewise, food selection and habitat complexity may also play an important role in distribution and abundance of marine organisms (Duffy and Hay 1991; Edgar and Robertson 1992).
Crustaceans exhibit one of the highest ranges of morphological diversity. Of these, it is believed that approximately 40% of all belongs to the group Peracarida (Kaestner 1980). Most peracarids are bottom-dwelling animals, either infaunal or epifaunal; they have a wide variety of feeding habits, i.e. surface deposit feeding, filter feeding, carnivory, omnivory and even foraminiferivory (Gudmundsson et al. 2000; De Broyer et al. 2003; Riisgard and Schotge 2007; Krapp et al. 2008; Guerra-García and Tierno de Figueroa 2009), and changes in food supply may influence the distribution of the species and the diversity patterns in the benthic environment. Furthermore, peracarids are being studied as bioindicators, since they have shown to be good indicators of environmental changes (Conradi and López-González 2001; Guerra-García and García-Gómez 2001; Ohji et al. 2002; Guerra-García and García-Gómez 2004; Dauvin and Ruellet 2007; Guerra-García et al. 2009a).
Given that this group lacks pelagic larvae and their capacities for long-distance movement are limited in adults, the studies on biogeography focused on this group have been numerous in recent years (e.g. Chavanich and Wilson 2000; Thiel 2002; Castellanos et al. 2003; De Broyer et al. 2003; Chiesa et al. 2005; Winfield et al. 2006; Myers and Lowry 2009). Nevertheless, research has not been so intensive in the Iberian Peninsula, and the knowledge in this field is still fragmentary (Bellan-Santini and Ruffo 1998; Guerra-García et al. 2009b, c, d) and mainly focused on the Strait of Gibraltar (Conradi et al. 1997; Castelló and Carballo 2001; Guerra-García and Takeuchi 2002). However, there has been a slight increase in the interest of this region during the last decade (e.g. Ballesteros 1988; Cruz et al. 2003; Pereira et al. 2006; Guerra-García et al. 2010). The Iberian Peninsula is located in the southwest of Europe and is the westernmost of the three major southern European peninsulas. Its coasts are washed by the Mediterranean on the eastern side and Atlantic on the northern and western side, converging at the Strait of Gibraltar.
Corallina elongata (hereafter C. elongata) is a macroalga belonging to the family Corallinaceae (Rhodophyta). This species is widely distributed, occurring not only all along Mediterranean (Flores-Moya et al. 1989; Conde et al. 1996; Bárbara and Cremades 1996; Babbini and Bressan 1997) and Atlantic (Guiry 1977; Neto 1994; Araujo et al. 2009), where it has been extensively reported, but also in the Pacific (Abbott 1999; Lee 2008). It is a whitish-pink to reddish-lilac calcified algae, with articulated fronds and fish-bone-like arrangement. Its axis is compressed and repeatedly pinnate from discoid base. Coralline algae can be considered as ecosystem engineers, since they can modify the environment by providing shelter from desiccation stress, wave action and predation, enriching biodiversity within its structure (Jones et al. 1994; Daleo et al. 2006). In extreme environments, intertidal coralline algal turfs ameliorate hard physical conditions, allowing the presence of many fauna that otherwise would not dwell at this level (Bertness et al. 2006). Corallina elongata was selected in this study, since it is one of the dominant macroalgae along the intertidal ecosystems of the whole Iberian Peninsula (Pérez-Cirera and Maldonado 1982; Guerra-García et al. 2006), and it was present in all sampling stations selected for the present work. Studies on biogeography of macrofauna associated with Corallina worldwide are scarce (Dommasnes 1969; Fernández and Niell 1987; Bitar 1984; Ballesteros 1988; Kelaher et al. 2001; Kelaher 2002; Kelaher and Castilla 2002; Kelaher et al. 2003; Bertness et al. 2006; Bussell et al. 2007; Liuzzi and López-Gappa 2008; Guerra-García et al. 2009b), especially in the Iberian Peninsula.
The main aim of this study was to demarcate the distribution and abundance patterns of benthic peracarids associated with the alga C. elongata in the intertidal zone along the whole coast of the Iberian Peninsula, and explore the relationship with some environmental variables such as oxygen concentration, turbidity, temperature, pH and conductivity
Materials and methods
Sampling was conducted in summer 2008 (June, July and August). The following environmental parameters were measured “in situ” at each sampling site: water temperature, pH, conductivity, dissolved oxygen and turbidity. Temperature and oxygen concentration were measured with an oxymeter CRISON OXI 45; pH and conductivity were measured using a conductivimeter-pHmeter CRISON MM40, and finally turbidity was measured in nephelometric turbidity units (ntu) using a turbidimeter WTW 335 IR. The seaweed C. elongata was selected as substrate, and three replicates (quadrats 20 × 20cm) were sampled in each station. Corallina elongata was distributed along the low intertidal level and sublittoral in most of stations, and the intertidal belt was selected for this study. The surface was scrapped, and the seaweed and associated fauna were collected. The samples were fixed in ethanol 80%, brought to laboratory and sieved using a mesh size of 0.5 mm. Peracarid crustaceans were sorted and identified to species level. Volume of C. elongata of each replicate was estimated as the difference between the initial and final volume when placed into a graduated cylinder with a fixed amount of water (see Pereira et al. 2006). Dry weight was also measured (after 24 h at 70°C). To estimate the cover of C. elongata in each locality, we used five random quadrats of 50 × 50 cm subdivided with thick fishing line into 25 square units of 10 × 10 cm. The presence/absence of the species was recorded for each unit, and data were expressed as cover percentage (mean ± SD of the 5 replicates).
Species richness (S), abundance (N), Shannon-Weaver diversity (H’) and Pielou’s evenness (J) were measured for each station. Possible differences in these parameters between Mediterranean and Atlantic stations were tested by one-way ANOVA, after verifying normality using the Kolmogorov–Smirnov test and the homogeneity of variances using the Levene test. To explore the species replacement along the Atlantic and Mediterranean gradients, the Whittaker index (Whittaker 1972) was calculated as measure of ß-diversity. The affinities among stations based on peracarid data were measured through cluster analysis using UPGMA method, based on the Bray-Curtis similarity index. The relationships between environmental measures and peracarid assemblages were studied by Canonical Correspondence Analysis (CCA) and BIO-ENV. Multivariate analyses were carried out using the PRIMER package (Clarke and Gorley 2001) and the PC-ORD programme (McCune and Mefford 1997), whereas for univariate analyses the SPSS programme was used.
Species were classified in geographical distribution groups (see also López de la Cuadra and García-Gómez 1994; Conradi and López-González 1999; Guerra-García et al. 2009b). For the present study, five groups were considered: I (Endemic Mediterranean), II (Atlantic and Mediterranean), III (Atlantic, absent in Mediterranean) IV (Atlantic, Mediterranean and Indo-Pacific) and V (Cosmopolitan)
Abiotic data and abundance patterns of C. elongata
Summary of the results of the CCA analysis
Percentage of species variance
Correlation with environmental variables
C. elongata cover (%)
The peracarid crustaceans constitute the dominant group of epiphytic macrofauna in the intertidal region (Guerra-García et al. 2010) and are useful as bioindicators (e.g. Conradi et al. 1997; Sánchez-Moyano and García-Gómez 1998; Guerra-García and García-Gómez 2001; Ohji et al. 2002; Dauvin and Ruellet 2007). On the other hand, C. elongata is one of the most important algae in the intertidal ecosystems (Pérez-Cirera and Maldonado 1982; Guerra-García et al. 2006). Consequently, the study of the peracarids associated with C. elongata in the Iberian Peninsula is especially relevant.
The most relevant aspect of this study lies on the faunistic contribution: seventy-eight species of peracarids have been identified during the present study, most of them widely distributed along the Atlantic and Mediterranean, and patterns of abundance along the whole Iberian Peninsula are also included (see Table 1). The percentage of Mediterranean endemics was very low (9%). These results agree with Guerra-García et al. (2009b), who studied the peracarids associated with C. elongata in the Strait of Gibraltar and found 40 species in the 25 selected stations. In the present study, we found 42 species in the 3 stations located in the Strait of Gibraltar (see stations 10, 11 y 12 in Fig. 1) with similar biogeographical distribution. The percentage of Mediterranean endemics is very low (3–5% for the Strait and 9% if we consider the whole Iberian Peninsula) when compared to other studies (see Bellan-Santini and Ruffo 1998; Conradi and López-González 1999; Guerra-García and Takeuchi 2002). The low number of Mediterranean endemics found for peracarids associated with C. elongata (see also Guerra-García et al. 2009b) contrast with the 37% of endemic amphipods reported by Bellan-Santini and Ruffo (1998), even higher than the 26.6% calculated by Fredj et al. (1992) for all the Mediterranean fauna as a whole. Conradi and López-González (1999) also reported a high endemic benthic Gammaridea fauna (18.3% endemics) from Algeciras Bay (Iberian side of the Strait of Gibraltar). Guerra-García et al. (2009b) explained this low endemicity on the basis of the distribution of C. elongata, which is an unspecific substrate widely distributed along the Atlantic and Mediterranean intertidal ecosystems. The peracarid fauna associated with this alga seems to have a low endemic component, but a high percentage of lessepsian species (group IV) due to colonization in progress by Indo-Pacific elements via the Suez Canal.
Multivariate analyses based on peracarid abundance clearly showed two groups of stations (Mediterranean vs. Atlantic) with stations of the Strait of Gibraltar clustered together with Mediterranean stations. This pattern was also obtained for the caprellid community associated with the seaweed Stypocaulon scoparium (see Guerra-García et al. 2009d), so the present study also reflects that the fauna of the Strait of Gibraltar seems to be more similar to the Mediterranean than to the Atlantic. In any case, along the Iberian Peninsula, the Strait is the area with higher rates of species replacement or turnover, as measured by the Whittaker index in the present study.
Among the physicochemical parameters, hydrodinamism and sedimentation rate are reported in literature as two of the most relevant factors to structure marine communities (Moore 1972; Dodds 1991; Gibbons 1988), together with temperature, conductivity, availability of food, predation and habitat structure (Duffy and Hay 1991; Dauby et al. 2001). In the present study, according to the CCA and BIO-ENV, conductivity was the variable which better explained peracarid distribution along the Iberian Peninsula. Mediterranean is characterized by higher conductivity and temperature and lower values of dissolved oxygen and turbidity. Tanaids showed preferences for Mediterranean stations, while isopods were more abundant in Atlantic stations. Amphipods did not show a clear general pattern as a group, since different species showed distinct distribution pattern. The unusual conditions measured in station 6 (low conductivity and oxygen and high turbidity) could be related to rivers influence discharging fresh water. These conditions seem to be excellent for some species, such as Parajassa pelagica. On the other hand, species of the genus Hyale were the most abundant in the present study. In fact, the genus Hyale is well adapted to life among algae of the higher littoral levels (Tararam et al. 1986; Baldinger and Gable 1995).
In the present study, although there were no significant differences in the number of species and Shannon diversity between Atlantic and Mediterranean stations, some species are substituted by others along the Atlantic-Mediterranean axis. Most of the substitution events affect species of the same genera, probably related to sympatric speciation. Some examples are the substitution of the species Jassa falcata (Atlantic) by J. cadetta (Mediterranean), Apherusa jurinei (Atlantic) by A. mediterranea (Mediterranean), Ampithoe helleri (Atlantic) by A. riedli (Mediterranean) or Stenothoe monoculoides (Atlantic) by S. tergestina (Mediterranean). Nevertheless, there are other factors that could also affect, such as competition or facilitation among species. For example, Viejo and Arrontes (1992) showed that the feeding activity of the isopod Dynamene bidentata was beneficial for the amphipod Hyale nilsonii, by providing suitable feeding surface on Fucus vesiculosus. A similar interaction seems to occur also in Tarifa Island between H. perieri, D. bidentata and the alga F. spiralis (Guerra-García et al. unpublished data). On the other hand, the higher Pielou index measured in the Mediterranean is probably due to high abundance values of some species in Atlantic stations such as Caprella penantis, Jassa falcata and Parajassa pelagica.
During the last decade, changes in the species distribution in marine ecosystems due to the climatic change are increasing (Francour et al. 1994; Walther et al. 2002; Macdonald et al. 2005; Harley et al. 2006; Barber et al. 2008). Further studies are necessary to explore whether observed patterns of the peracarid species are strictly consequence of natural factors or are already affected by the climatic change.
Financial support of this work was provided by the Ministerio de Educación y Ciencia (Project CGL2007-60044/BOS) co-financed by FEDER funds and by the Consejería de Innovación, Ciencia y Empresa, Junta de Andalucía (Project P07-RNM-02524). Special thanks to J. Corzo, M.P. Cabezas and E. Baeza-Rojano for their collaboration during the sampling programme and to J.E. Sánchez-Moyano for his assistance in species identification.
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