# Community Structure and Distribution Pattern of Intertidal Invertebrate Macrofauna at Some Anthropogenically Influenced Coasts of Kathiawar Peninsula (India)

Authors: Poonam Bhadja; Paresh Poriya; Rahul Kundu
Journal: Advances in Ecology
 (2014)

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## Abstract

Present communication reports the community structure and distribution pattern of intertidal invertebrate macrofauna at four shores of the Kathiawar peninsular coastline off the Arabian Sea (India). The selected shores have different levels of human activities. Present report tests three hypotheses; that is, (i) distribution of invertebrate macrofauna in these shores is influenced by space and time, (ii) abiotic factors have a profound influence on the distribution pattern of intertidal macrofaunal assemblages, and (iii) human activities influence the community structure of the intertidal invertebrate macrofauna at these shores. To test these hypotheses, spatiotemporal variations in different ecological indices were studied. A total of 60 species from six phyla were considered for the study. High species diversity was recorded during winter and monsoon seasons in almost all the shores studied. It was also evident that a few environmental factors had a cumulative influence on the distribution pattern of intertidal macrofauna. Significant spatial variations in the species diversity and evenness were also observed. Though the shores studied have similar coast characteristics and climatic conditions, they face different levels of human activities. Therefore, the observed variations in the intertidal faunal assemblage were possibly caused by anthropogenic stress.


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## Body

## 1. Introduction

Rocky shores are the most extensive littoral habitats exposed to eroding waves and, thus, are ecologically very important [1]. Among that, invertebrate communities of rocky shores function as integrators of ecological processes over time scale [2, 3]. The communities act as a bioindicator and may be monitored to assess ecological change due to anthropogenic actions [4, 5]. Anthropogenic stress is the response of biological entity, of any individual, population, or community, to an anthropogenic disturbance. This stress at one level of organization may also have an impact on another level. Since it is difficult to detect the effects of anthropogenic stress at the individual organismic level, they are more often investigated at a population or community level [1]. Pielou [6] and Magurran [7] reported that the measures of species diversity play a central role in ecology and conservation biology. Benthic habitat is complex and many of the environmental factors that influence macroinvertebrate assemblage structure are interrelated [8, 9]; thus, identifying a single environmental factor as most important in structuring assemblages is challenging. Intertidal invertebrates and macroalgae occupy low trophic levels and are responding quicker to alterations in climate than species at higher trophic levels [10]. They often show the first response in a cascade of effects up the food chain and are therefore important sentinels of climate change impacts [11]. In addition to temperature, several other climate-related drivers are also impacting and have adverse effects upon coastal habitats including sea level rise, increases in relative wave height and storminess, and the associated secondary effects arising from adaptation and mitigation activities in coastal regions [12].Macrobenthic invertebrates are useful bioindicators providing a more accurate understanding of changing aquatic conditions than chemical and microbiological data, which at least give short-term fluctuations [4–9, 13]. Their composition, abundance, and distribution can be influenced by water quality [14, 15]. They all stated that variations in the distribution of macrobenthic organisms could be a result of differences in the local environmental conditions [15]. However, the composition, abundance, and distribution of invertebrate macrofauna in the rocky intertidal zones are generally influenced by water quality [5, 16, 17]. Understanding the relative importance of environmental factors in structuring assemblages is important because benthic macroinvertebrates are used more than any other organisms to assess the condition of streams and identifying the factors primarily associated with altered macroinvertebrate assemblages is necessary before restoration action can begin.The coastline of Kathiawar Peninsula is significantly rocky with irregular patches of sand or mud. Veraval and Mangrol are the two developed fishing ports with allied installations which handle 62% of fish catch for several export oriented fish processing units located in the vicinity. Apart from existing ports that facilitate import or export of fish and fishery products, this coastal area is also dominated by large industries like rayon, cement, food and fodder processing, fertilizers, salt, cement, soda ash, and lime stone associated industries. Tourism is also another related human activity which directly affects the intertidal zones of the Kathiawar Peninsula. Thus, studies on the current ecological status of the macrofaunal assemblage in this industrially significant coastline are very important from ecological and conservation points of view. Therefore, the present communication is relevant not only for this particular region but also for any other coastline with similar conditions.The present communication reports the ecological status of various intertidal invertebrate faunal groups of the rocky and rocky-muddy intertidal areas at South Saurashtra coastline off the Arabian Sea. It also reports the community structure of the intertidal zones in relation to abiotic factors and anthropogenic activities. Present report tests the hypotheses that (i) there is a spatiotemporal influence on the distribution pattern of different invertebrate phyla at the selected shores along this continuous coastline, (ii) abiotic factors influence the intertidal macrofaunal assemblages of the shores that are on the open sea coastline, and (iii) human activities have a profound influence on the gross community structure of the intertidal faunal assemblages at these open sea shores.


## 2. Materials and Methods

### 2.1. Study Location

For this study, four sampling sites, namely, Dwarka (22°13′N, 68°58′E), Mangrol (21°07′N, 70°07′E), Veraval (20°53′N, 70°26′E), and Kodinar (20°46′N, 70° 46′E) were selected (Figure1). These sites were chosen on the basis of their strategic locations for industries and related infrastructural facilities and different anthropogenic activities along the entire coastal area. Dwarka is a major Hindu pilgrim town and a tourist place with low human activities on the coast. The intertidal belt of Dwarka consists of large rocks and boulders causing resistance to upcoming wave and, hence, generates harsh water splash. Mangrol is a small hamlet with a fish landing jetty and few small scale fisheries related industries. This site is experiencing medium anthropogenic pressure on the coast. The entire intertidal belt of Mangrol is interspersed with numerous tide pools, puddles, crevices, and channels with intermittent sandy patches. On the other hand, Veraval is the largest fish landing site of India, surrounded by many fish processing plants and large industrial units. The substratum of the intertidal zones at Veraval is mainly rocky-sandy with few muddy patches. Kodinar is a small industrial town with large cement and sugar industries located near the coastline. The intertidal zone of Kodinar is made up of hard flat rocky substratum having small sized depressions interspersed with pools and puddles. Veraval and Kodinar shores are considered as high anthropogenic pressure zones.Figure 1
Map showing the study locations along the South Saurashtra coastline off the Arabian Sea.


### 2.2. Field Sampling

Studies on the macrofaunal diversity and seawater quality (in triplicate) from the intertidal regions of these sites were carried during November 2008 to October 2009. The entire intertidal belt of each sampling site was subdivided into three vertical zones. The macrofaunal diversity and distribution in the intertidal belt at each station were studied during the low tide by quadrat method [18]. Quadrat of 0.25 m2 was laid along the employed line transect at every 10 m interval on the intertidal region. A minimum of ten quadrates were laid in a criss-cross direction at the intertidal belt to cover the maximum exposed area. For water quality, previously published data of different seawater quality parameters were considered [17].


### 2.3. Data Analysis

Each study site was sampled monthly for quantitative analysis of intertidal macrofauna. The monthly data from the study sites were integrated as a seasonal dataset as the weather condition of this part of the peninsular India typically represents the periods of winter (December to February), summer (March to May), monsoon (June to August), and post-monsoon (September to November) seasons. Diversity of the macrofauna was determined using Shannon-Wiener index [19] and Pielou’s index (J) of evenness and Menhinick index (d) of species richness was applied to calculate the diversity as per Odum [20]. The Shannon Index (H
′) was calculated by the formula H
′
=
-
(
Pi
×
ln
⁡
Pi
), where Pi is the fraction of the ith species of total fauna. Pielou’s evenness (J
′) was calculated by the formula J
′
=
H
′
/
ln
⁡
S, where H
′ is the Shannon index as defined above and S is the number of species observed. Species richness (d) is based on the number of species present in a community (S) and incorporates the total number of individuals in the community (N). The species richness was calculated by the formula d
=
S
/
N.Two-factor analysis of variance (ANOVA) was employed to estimate the spatiotemporal variations in diversity, evenness, and richness values. Correlation coefficients analysis was also done to assess the influence of abiotic factors on the macrofaunal community structure [21]. Bray-Curtis similarity analysis was performed on the species diversity data to detect multivariate spatial similarities. All statistical analyses were done as per Sokal and Rohlf [22].


## 2.1. Study Location

For this study, four sampling sites, namely, Dwarka (22°13′N, 68°58′E), Mangrol (21°07′N, 70°07′E), Veraval (20°53′N, 70°26′E), and Kodinar (20°46′N, 70° 46′E) were selected (Figure1). These sites were chosen on the basis of their strategic locations for industries and related infrastructural facilities and different anthropogenic activities along the entire coastal area. Dwarka is a major Hindu pilgrim town and a tourist place with low human activities on the coast. The intertidal belt of Dwarka consists of large rocks and boulders causing resistance to upcoming wave and, hence, generates harsh water splash. Mangrol is a small hamlet with a fish landing jetty and few small scale fisheries related industries. This site is experiencing medium anthropogenic pressure on the coast. The entire intertidal belt of Mangrol is interspersed with numerous tide pools, puddles, crevices, and channels with intermittent sandy patches. On the other hand, Veraval is the largest fish landing site of India, surrounded by many fish processing plants and large industrial units. The substratum of the intertidal zones at Veraval is mainly rocky-sandy with few muddy patches. Kodinar is a small industrial town with large cement and sugar industries located near the coastline. The intertidal zone of Kodinar is made up of hard flat rocky substratum having small sized depressions interspersed with pools and puddles. Veraval and Kodinar shores are considered as high anthropogenic pressure zones.Figure 1
Map showing the study locations along the South Saurashtra coastline off the Arabian Sea.


## 2.2. Field Sampling

Studies on the macrofaunal diversity and seawater quality (in triplicate) from the intertidal regions of these sites were carried during November 2008 to October 2009. The entire intertidal belt of each sampling site was subdivided into three vertical zones. The macrofaunal diversity and distribution in the intertidal belt at each station were studied during the low tide by quadrat method [18]. Quadrat of 0.25 m2 was laid along the employed line transect at every 10 m interval on the intertidal region. A minimum of ten quadrates were laid in a criss-cross direction at the intertidal belt to cover the maximum exposed area. For water quality, previously published data of different seawater quality parameters were considered [17].


## 2.3. Data Analysis

Each study site was sampled monthly for quantitative analysis of intertidal macrofauna. The monthly data from the study sites were integrated as a seasonal dataset as the weather condition of this part of the peninsular India typically represents the periods of winter (December to February), summer (March to May), monsoon (June to August), and post-monsoon (September to November) seasons. Diversity of the macrofauna was determined using Shannon-Wiener index [19] and Pielou’s index (J) of evenness and Menhinick index (d) of species richness was applied to calculate the diversity as per Odum [20]. The Shannon Index (H
′) was calculated by the formula H
′
=
-
(
Pi
×
ln
⁡
Pi
), where Pi is the fraction of the ith species of total fauna. Pielou’s evenness (J
′) was calculated by the formula J
′
=
H
′
/
ln
⁡
S, where H
′ is the Shannon index as defined above and S is the number of species observed. Species richness (d) is based on the number of species present in a community (S) and incorporates the total number of individuals in the community (N). The species richness was calculated by the formula d
=
S
/
N.Two-factor analysis of variance (ANOVA) was employed to estimate the spatiotemporal variations in diversity, evenness, and richness values. Correlation coefficients analysis was also done to assess the influence of abiotic factors on the macrofaunal community structure [21]. Bray-Curtis similarity analysis was performed on the species diversity data to detect multivariate spatial similarities. All statistical analyses were done as per Sokal and Rohlf [22].


## 3. Results

### 3.1. Abiotic Factors

Seasonal changes in various physicochemical parameters of seawater at the four selected locations are shown in Figure2. Regarding the measures taken for the environmental parameters, it was observed that amongst the abiotic factors, highest mean water temperature was recorded during summer at all the coasts studied (Figure 2(a)). The pH value showed a similar trend and was found low during the monsoon (Figure 2(b)). The salinity was found to be high during summer and low during the winter at almost all the sampling sites (Figure 2(d)). Dissolved oxygen level was high during the post-monsoon season (6.14 to 6.38 mg/L) at almost all the sampling sites. Relatively lower dissolved oxygen level was observed during winter than the post-monsoon (Figure 2(e)). The seawater turbidity was relatively constant during monsoon to post-monsoon, ranging from 4.5 to 5.1 NTU at all the sampling sites (Figure 2(c)). High chlorophyll level was observed during winter which decreased to the minimum during summer (Figure 2(f)).Seasonal variations in the seawater quality parameters of the coasts studied. Error bars represent standard deviation over mean values.
(a)
(b)
(c)
(d)
(e)
(f)


### 3.2. Macrofaunal Community Structure

In the present study a total of 60 different invertebrate macrofaunal species were identified from the intertidal regions of the sampling sites. These species belonged to different groups like 3 species of Porifera, 8 species of Coelenterata, 5 species of Annelida, 6 species of Arthropoda, 35 species of Mollusca, and 3 species of Echinodermata. Molluscan forms were the most common and dominant species followed by Coelenterate, Arthropoda, and Annelida at all the sampling stations (Figure6). The levels of diversity, richness, and evenness indices of all these invertebrate groups were analyzed and given in Figures 3–5. Diversity (Shannon-Wiener index [19]) values ranged from 0.01 during winter to 2.09 during summer at Mangrol. The value of diversity indices of phylum Porifera varied from 0.07 to 0.27 during summer and monsoon seasons at Mangrol and Kodinar, respectively. In general, the species diversity of phylum Coelenterata was comparatively low at almost all the sampling sites. However, it showed moderate diversity values at Dwarka during monsoon season. Highest species diversity of this group was recorded at Veraval during winter season (Figure 3). Shannon H
′ values were high at Mangrol and Dwarka during winter and summer seasons, but were found to be low at other locations. Significant temporal variations in the total species diversity were observed in three groups (phyla Annelida, Arthropoda, and Mollusca) (Table 1). The total diversity of phylum Echinodermata did not show any significant variations possibly due to the fact that these animals generally prefer the lower littoral zone which is comparatively less affected by the changing environmental factors. Similarly, Porifera and Arthropoda also showed significant temporal variations in species richness (Table 1). However, when the diversity values of all macrofauna from all phyla are pooled together, significant spatial variations are shown. The observed spatial variations in the species evenness (J
′) were found to be more during the post-monsoon followed by the monsoon and winter seasons (Figure 5). The minimum evenness was observed in Echinodermata during winter and maximum evenness was in Coelenterata during monsoon season. Though high species richness was observed in echinoderms, its evenness was the lowest amongst all groups studied (Figures 4 and 5). High species richness and evenness were observed in Mollusca followed by annelids, sponges, and arthropods (Figures 4 and 5). Results of the two-factor ANOVA showed significant temporal variations in species richness of Porifera and Arthropoda (Table 1). Similarly, spatiotemporal variations in the species evenness were observed only in phylum Mollusca, whereas only temporal variations were observed in case of phylum Arthropoda (Table 1). Similar results were also observed in the dendrogram showing the similarity in the macrofaunal diversity of all species combined between the selected shores (Figure 7).Table 1
Results of the two-way ANOVA (without replication) of the mean seasonal Shannon-Wiener diversity (H
′), richness (d), and evenness (J
′) values of the six invertebrate phyla sampled at the four stations.
Animal group
Source of variation
F values
H
′
d
J
′
Porifera
Station
18.32*
3.09
4.55*
Season
7.91*
5.25*
1.57
Coelenterata
Station
7.65*
2.52
2.30
Season
7.71*
0.93
2.40
Annelida
Station
1.17
2.11
2.89
Season
6.08*
2.82
13.11*
Arthropoda
Station
0.72
2.95
3.65
Season
11.30*
10.90*
10.14*
Mollusca
Station
3.49
1.36
4.17*
Season
18.67*
3.12
14.83*
Echinodermata
Station
0.75
2.09
0.17
Season
1.73
3.15
1.25
*Significant at P
=
0.05 level; tabulated F value at df 15
=
3.86.Figure 3
Seasonal variations in the Shannon-Wiener diversity (H
′) of major intertidal phyla from all three littoral zones. Note the change of scale in different coasts studied.Figure 4
Seasonal variations in the species richness (d) of major intertidal phyla from all three littoral zones.Figure 5
Seasonal variations in the species evenness (J
′) of major intertidal phyla from all three littoral zones.Figure 6
Comparative histograms showing Shannon-Wiener diversity (H
′) values between phylum Mollusca and all other phyla pooled together.Figure 7
Dendrogram showing similarity in the macrofaunal diversity of all species combined between the selected shores.


## 3.1. Abiotic Factors

Seasonal changes in various physicochemical parameters of seawater at the four selected locations are shown in Figure2. Regarding the measures taken for the environmental parameters, it was observed that amongst the abiotic factors, highest mean water temperature was recorded during summer at all the coasts studied (Figure 2(a)). The pH value showed a similar trend and was found low during the monsoon (Figure 2(b)). The salinity was found to be high during summer and low during the winter at almost all the sampling sites (Figure 2(d)). Dissolved oxygen level was high during the post-monsoon season (6.14 to 6.38 mg/L) at almost all the sampling sites. Relatively lower dissolved oxygen level was observed during winter than the post-monsoon (Figure 2(e)). The seawater turbidity was relatively constant during monsoon to post-monsoon, ranging from 4.5 to 5.1 NTU at all the sampling sites (Figure 2(c)). High chlorophyll level was observed during winter which decreased to the minimum during summer (Figure 2(f)).Seasonal variations in the seawater quality parameters of the coasts studied. Error bars represent standard deviation over mean values.
(a)
(b)
(c)
(d)
(e)
(f)


## 3.2. Macrofaunal Community Structure

In the present study a total of 60 different invertebrate macrofaunal species were identified from the intertidal regions of the sampling sites. These species belonged to different groups like 3 species of Porifera, 8 species of Coelenterata, 5 species of Annelida, 6 species of Arthropoda, 35 species of Mollusca, and 3 species of Echinodermata. Molluscan forms were the most common and dominant species followed by Coelenterate, Arthropoda, and Annelida at all the sampling stations (Figure6). The levels of diversity, richness, and evenness indices of all these invertebrate groups were analyzed and given in Figures 3–5. Diversity (Shannon-Wiener index [19]) values ranged from 0.01 during winter to 2.09 during summer at Mangrol. The value of diversity indices of phylum Porifera varied from 0.07 to 0.27 during summer and monsoon seasons at Mangrol and Kodinar, respectively. In general, the species diversity of phylum Coelenterata was comparatively low at almost all the sampling sites. However, it showed moderate diversity values at Dwarka during monsoon season. Highest species diversity of this group was recorded at Veraval during winter season (Figure 3). Shannon H
′ values were high at Mangrol and Dwarka during winter and summer seasons, but were found to be low at other locations. Significant temporal variations in the total species diversity were observed in three groups (phyla Annelida, Arthropoda, and Mollusca) (Table 1). The total diversity of phylum Echinodermata did not show any significant variations possibly due to the fact that these animals generally prefer the lower littoral zone which is comparatively less affected by the changing environmental factors. Similarly, Porifera and Arthropoda also showed significant temporal variations in species richness (Table 1). However, when the diversity values of all macrofauna from all phyla are pooled together, significant spatial variations are shown. The observed spatial variations in the species evenness (J
′) were found to be more during the post-monsoon followed by the monsoon and winter seasons (Figure 5). The minimum evenness was observed in Echinodermata during winter and maximum evenness was in Coelenterata during monsoon season. Though high species richness was observed in echinoderms, its evenness was the lowest amongst all groups studied (Figures 4 and 5). High species richness and evenness were observed in Mollusca followed by annelids, sponges, and arthropods (Figures 4 and 5). Results of the two-factor ANOVA showed significant temporal variations in species richness of Porifera and Arthropoda (Table 1). Similarly, spatiotemporal variations in the species evenness were observed only in phylum Mollusca, whereas only temporal variations were observed in case of phylum Arthropoda (Table 1). Similar results were also observed in the dendrogram showing the similarity in the macrofaunal diversity of all species combined between the selected shores (Figure 7).Table 1
Results of the two-way ANOVA (without replication) of the mean seasonal Shannon-Wiener diversity (H
′), richness (d), and evenness (J
′) values of the six invertebrate phyla sampled at the four stations.
Animal group
Source of variation
F values
H
′
d
J
′
Porifera
Station
18.32*
3.09
4.55*
Season
7.91*
5.25*
1.57
Coelenterata
Station
7.65*
2.52
2.30
Season
7.71*
0.93
2.40
Annelida
Station
1.17
2.11
2.89
Season
6.08*
2.82
13.11*
Arthropoda
Station
0.72
2.95
3.65
Season
11.30*
10.90*
10.14*
Mollusca
Station
3.49
1.36
4.17*
Season
18.67*
3.12
14.83*
Echinodermata
Station
0.75
2.09
0.17
Season
1.73
3.15
1.25
*Significant at P
=
0.05 level; tabulated F value at df 15
=
3.86.Figure 3
Seasonal variations in the Shannon-Wiener diversity (H
′) of major intertidal phyla from all three littoral zones. Note the change of scale in different coasts studied.Figure 4
Seasonal variations in the species richness (d) of major intertidal phyla from all three littoral zones.Figure 5
Seasonal variations in the species evenness (J
′) of major intertidal phyla from all three littoral zones.Figure 6
Comparative histograms showing Shannon-Wiener diversity (H
′) values between phylum Mollusca and all other phyla pooled together.Figure 7
Dendrogram showing similarity in the macrofaunal diversity of all species combined between the selected shores.


## 4. Discussion

Anthropogenic disturbances can affect the physiological state of the animals, which may result in changes of processes, such as rates of growth [23, 24], and disturbances affect recruitment [25, 26] or mortality [25, 27] and, therefore, are most easily identified as differences in the numbers and types of animals found in disturbed or undisturbed sites [28–30]. In the long history of the marine biological research, together with habitat structure, food availability, and predation, physicochemical parameters like temperature, pH, conductivity, BOD, COD, and so forth are determining factors in structuring different marine assemblages [31–34]. The environmental factors, as the highest surface water temperature was recorded during summer, are influenced by the intensity of solar radiation, evaporation, freshwater influx, and cooling; summer peaks and monsoon troughs in air and water temperature were found similar to reported values for west coast of India by Arthur [35]. The low pH value during the monsoon was probably due to the cumulative influence of freshwater influx, dilution of saline water with rain, and reduction of salinity and temperature. Seasonal variations in the salinity observed in the present study influenced the fauna and, thus, were the limiting factor for the distribution of living organisms in the intertidal region [36–38]. Higher dissolved oxygen level might be due to the rough weather conditions during monsoon season [39, 40]; however, lower dissolved oxygen level observed during winter is typical for the coastline studied [5, 17, 41]. The seawater turbidity was constant during monsoon possibly due to the mixing of rainwater runoff with seawater during monsoon season prevailing in this area [42]. High turbidity might have affected the species composition and community structure of marine macrobenthos in the intertidal region [42]. The trend of higher chlorophyll level was possibly in association with the northern Arabian Sea winter cooling phenomena [17, 43, 44].The results indicated that wide substratum preference, adaptational capabilities against changing environmental conditions and mobility to avoid harsh conditions have played possible roles [42]. The results of the two-factor ANOVA showed that only two faunal groups (Porifera and Coelenterata) showed spatiotemporal variations in the total diversity (Table 1) possibly due to fluctuations in the environmental factors and changing anthropogenic pressure. Khan et al. [45] reported higher Shannon diversity index, in the range of 2.5–3.5, as a healthy condition for this coastline. In the present study, the diversity indices were comparatively low at Veraval and Kodinar during the study period possibly due to the fluctuations in the environmental conditions and high human interference in the coastal area. It is possible that being predominantly rocky, the selected coasts harbor more species of the dominant phyla having moderate to high level of species richness typical for rocky intertidal assemblage [46]. Results of the present investigation showed high species richness and low species evenness in almost all the selected sampling sites. However, the observed low species evenness (Figure 5) was possibly due to the flatness of the intertidal areas exposed during low tide [41]. It is apparent from the present study (Table 2) that the species richness and evenness were influenced by environmental factors and were inversely correlated with anthropogenic disturbances [5]. High species richness recorded during the winter season at some of the study sites might be due to stable environmental factors that play an important role in faunal distribution [47–49].Table 2
Results of single factor ANOVA for the Shannon diversity (H
′), richness (d), and evenness (J
′) of major macrofaunal phyla at four shores studied.
F values
H
′
d
J
′
Porifera
1.4851
3.4466
0.8312
Coelenterata
2.8945
0.6714
1.8127
Annelida
5.8276*
2.2063
8.8955*
Arthropoda
12.1567*
7.3309*
6.0997*
Mollusca
11.5069*
2.8561
8.2687*
Echinodermata
1.8437
2.4773
1.5767
Total
8.9924
*
1.9827
1.0613
*Significant at P
=
0.05 level; tabulated F value = 3.49.The correlation coefficient analysis between the species richness and abiotic factors showed variations amongst different groups as well as within different parameters. Significant variations in the species richness of annelids with salinity were observed at Veraval and Kodinar (r
=
0.96 and 0.94, resp.) possibly due to influx of freshwater runoff in these shores during monsoon. Molluscan forms and sponges were correlated with variations in DO at Mangrol (r
=
0.97 and 0.99, resp.) and Kodinar (r
=
0.95 and 0.98, resp.). Variations in the salinity, dissolved oxygen, and turbidity were reported to affect the near shore environment [50–54]. The variations in the abiotic factors and human interference, thus, lead to the presence of a diverse range of habitats in these waters which are often characterized by distinct faunal assemblages [55–59]. Ingram and Lin [53] reported that species diversity directly correlates with the concentration of chlorophyll. In this study, Annelida were found to be associated with different levels of chlorophyll at Dwarka, Veraval, and Kodinar (r
=
0.92, 0.92, and 0.96, resp.). In case of species evenness, the macrofaunal groups were clearly influenced by few abiotic factors. In the present study, high correlation coefficient was observed in case of sponges at Veraval (r
=
0.93) and Kodinar (r
=
0.97), possibly due to the industrial effluents and sewage disposal, which might have influenced the pH level of the area under study. Similar observations were evident in case of Coelenterata (r
=
0.96) and Arthropoda (r
=
0.97) at Veraval and Echinodermata (r
=
0.96) at Mangrol. There was a significant positive correlation between the dissolved oxygen level and species richness of sponges at Mangrol (r
=
0.96) and Kodinar (r
=
0.96) and, in case of Arthropoda, at Dwarka (r
=
0.98) and Kodinar (r
=
0.93). The results of the correlation coefficient clearly indicated that the species richness and evenness were lowest at sites that also had the highest anthropogenic activities [41]. Amongst the four coasts studied, Veraval and Kodinar were highly influenced by anthropogenic pressure, whereas, in Dwarka and Mangrol, the human influence was less (Figure 7) [17, 60–62].


## 5. Conclusions

Results of the present study indicated that there were no significant spatial variations in the species diversity of major macrofaunal phyla. This is possibly due to the fact that the shores studied are situated along the same continuous coastline and share common coast characteristics. Significant temporal variations in the faunal diversity of few phyla were observed indicating that the varying environmental factors do have a cumulative influence on the distribution pattern of the benthic organisms. Interestingly, significant variations in the species diversity, richness, and evenness were observed in Veraval and Kodinar where the coast characteristics and climatic conditions were almost identical. Therefore, it may be possible that though the selected four shores share similar coast characteristics and climatic conditions, the variations in the intertidal assemblage were influenced by human activities. It appears that Veraval and Kodinar coasts were highly affected by the anthropogenic pressure followed by Mangrol and Dwarka coasts, where the human influences on the intertidal were minimum. Appropriate conservational strategies should be taken to minimize the anthropogenic pressure on the affected coastal areas to maintain the rich and diverse rocky intertidal biota of this region.



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*Source: 547395-2014-08-06.xml*