Intertidal Reef Assessment on the Fleurieu Peninsula, S.A.
REPORT TO THE S.A. DEPARTMENT OF ENVIRONMENT AND HERITAGE
JUNE 2007
Kirsten Benkendorff* and Daniel Thomas
School of Biological Sciences, Flinders University, GPO Box 2100, Adelaide, SA, 5001.
* Author for correspondence: Ph (08) 8201 3959; Fax (08) 8201 3015;
Email [email protected]
Summary
Biodiversity and habitat surveys of the physical environment were conducted at 17 intertidal sites along the Fleurieu Peninsula S.A. Species inventories revealed 112 species of molluscs, 29 echinoderms and 49 marine plants across all sites. A hotspot for molluscan diversity was located at Kings Beach at the tip of the
Peninsula, whereas a hotspot for echinoderms occurred at Myponga and for algae at Hallett Cove within the Gulf of St Vincent. Sites within the Aquatic reserves at Port Noarlunga and Aldinga Reef were found to have a significantly lower mean species richness for invertebrates (p value = 0.015 ) compared to sites outside the reserves. This could be partly related to rock type, as all sites within the reserves was composed of soft limestone, whereas significantly higher
species richness was found on the harder crystalline, igneous and metamorphic rock types (invertebrates p = 0.007, flora p = 0.031). Multivariate analyses revealed significantly different molluscan communities occur on the two rock types (p value = 0.004). Species richness of invertebrates and algae were found to be significantly correlated (p = 0.028), but there were no significant
correlations between species richness and the number of habitats, habitat complexity or percent cover of sessile organisms found. Consequently, habitat data can not be used as a surrogate for prioritizing sites for biodiversity
conservation. However, adequate protection for hard intertidal rocky reefs, such as the invertebrate hotspots, should be considered for future marine planning in this region.
Introduction
Intertidal reefs (rocky shores) are important ecosystems along the
coastline of the Fleurieu Peninsula, S.A. They support complex communities of algae and invertebrates, which have adapted to survive the harsh extremes of the constantly changing physical environment. Southern Australian temperate marine flora and fauna is well known for high biodiversity and a large proportion of endemic species (Zann 2000). Nevertheless, the communities occurring on intertidal reefs in South Australia have been more or less neglected since Womersley and Thomas’s (1976) account in the original volume of “The Natural History of the Adelaide Region” (adapted from Womersley and Edmonds, 1958
study), with the exception of several unpublished student theses (e.g. Williams 1996; Pocklington 2003; Cantin 2005; Dutton 2007; Liversage 2007).
In the “No Species Loss” biodiversity policy, the S.A. Government (2006) has recognized the need to identify and fill gaps in the scientific knowledge and understanding of our biodiversity. Under Strategic Area III, Target 21 identifies the need for systematic surveys of marine plants and animals. Species inventory data provides the foundation for conservation and management of marine
habitats (Benkendorff and Davis 2002; Gladstone 2002). It provides baseline data for characterizing and monitoring the state of the environment. Strategic area III of the No Species Loss Policy (S.A. Government 2006) further
recognizes the need to identify priority areas of high conservation value for biodiversity planning. Species inventory data collected using rapid biodiversity assessment (1hr timed search surveys) has been validated for prioritising intertidal reefs for their biodiversity (Benkendorff, 2003) and can facilitate the identification of biodiversity hotspots (e.g. Benkendorff 2005). Benkendorff and Davis (2002), define biodiversity hotspots as sites with more than two standard deviations above the mean species richness for a region. These sites may be considered a priority for efficient protection of a broad range of species.
Multivariate analyses of species occurrence data can also be used to identify distinct ecological communities (e.g. Benkendorff 2005) and thus facilitate the process of ensuring representativeness within a network of marine reserves.
Ecological communities on intertidal reefs can be influenced by a range of different biotic and abiotic interactions. The Habitat Diversity Hypothesis (Connor and McCoy, 1979), predicts that a greater diversity of species will occur where a greater diversity of habitats exist. Consequently, habitat diversity has been used as a surrogate for intertidal reef biodiversity in NSW (NSW Fisheries 2001).
Other features that could influence the diversity of species found include rock type (e.g. Cattaneo-Vietti et al., 2002; Guidetti et al. 2004) and habitat complexity (e.g. McGuinness and Underwood 1986; Benkendorff 2005). For example, the presence of complex boulder fields in shallow pools provides good habitat for many sessile invertebrates and the deposition of molluscan egg masses (Benkendorff et al., 2005). However, it is currently unclear if these abiotic measures will be useful for characterization of S.A. intertidal reefs.
The principle aim of this project was to provide a preliminary assessment of intertidal reefs along the Fleurieu Peninsula, S.A. Specifically, the abiotic characteristics of 17 intertidal reefs were assessed, including substrate type, rock type and substrate complexity. Information on percent cover of sessile organisms was also collected. Baseline species inventory data was collected for algae, molluscs and echinoderms from all selected sites. Molluscs have previously been established as good indicators for other invertebrates on temperate intertidal reefs in Australia (Gladstone 2002). They are also the most dominant and conspicuous intertidal organisms, they represent the full range of tropic niches and they can be relatively easily identified compared to other invertebrates
(Benkendorff and Davis 2002). However, molluscan diversity has been shown not to correlate with algal diversity (Gladstone 2002; Cantin 2003) and
consequently independent surveys are required for these primary producers on intertidal reefs. Furthermore, preliminary surveys have found no correlation between echinoderms and molluscs on South Australian reefs (Cantin 2003;
Benkendorff 2005).
These surveys have been used to provide a preliminary assessment of the physical environment and relative species richness found at different intertidal reefs around the Fleurieu Peninsula. However, the species inventories should not be taken as a comprehensive species list for the area, due to the limited time frame of the project. Intertidal community composition has been compared across the different sites, with a preliminary assessment of relationships to abiotic habitat characteristics. This later point has been followed up in more detail, particularly with respect to rock type, for a subset of sites in the Honours thesis by Dutton (2007).
Methods
In total 17 sites were selected for surveys along the Fleurieu Penninsula, S.A. (Figure 1). Due to the size of the intertidal reef within the Aquatic reserve at Aldinga, two sites were located on this reef over 100m apart. At each site a 20 x 20 m plot was established using tape measures and corner markers. Due to the relatively small patches of rock found near Port Noarlunga Jetty, two small reefs
with a total length of 20m were combined for the survey at this location. A GPS location was taken from approximately the middle of each plot. A summary of the survey dates, weather and tidal conditions and the exact locations for each survey site is provided in Table 1. All surveys were undertaken between
November 2006 to early March 2007 during low tide (<0.3m). At each site basic observational data was collected on the rock type and type of habitats present.
Substrate Transect Sampling
Five randomly-spaced 20 m shore-normal line transects were located within each study site using a 50 m fiberglass tape. Substrate types and percent coverage of sessile organisms occurring in patches greater than 5 cm in length were visually observed along the transects using the line intercept method. The extent of each substrate was recorded in centimeters, then summed and divided by the total length (20m) to obtain the percent cover. The following classifications were used for substrates and sessile organisms:
Substrates:
exposed rock submerged rock
exposed boulders submerged boulders
exposed pebbles submerged pebbles
exposed sand submerged sand
- boulders were classed as larger than fist-sized
- where boulders exceeded approximately 1 m along their longest axis they were classed as rock
- submerged substrates were covered with at least 5 cm of seawater at low tide
Sessile Organisms:
foliose algae mussels
turfing algae galeolaria crust
encrusting
algae/lichen mixed community
seagrass barnacles
- encrusting algae and lichen were classed together.
- mixed communities consisted of high-density mussel concentrations on mats of turfing algae where the species ratio was visually observed to approach
approximately 20/80 percent in either direction.
Complexity
Substrate complexity was determined by aligning a 10 m chain (link size = 23mm) along each transect and pushing it into all cracks and crevices to closely contour the vertical profile of the substrate. The horizontal distance reached by the chain was recorded and used to calculate substrate complexity by the ratio of the substrate contour length (X < 10m) to total linear length (10m). Ratios
approaching 1 are almost flat, whereas those closer to zero are highly rugose.
Species Inventories
At each site a 1hr timed-search survey was conducted for molluscs and echinoderms. Species were recorded within 10 minute time intervals to enable construction of species accumulation curves. All available habitats were
thoroughly searched within each 20 x 20m plot. At the completion of each survey each species was assigned a semi-quantitative abundance ranking whereby;
rare < 5, uncommon = 6-20, common = 21-100 and abundant >100 individuals per site. The species were identified in the field where possible and voucher specimens or photographs were used for further confirmation. Molluscs were identified according to Lamprell & Healy (1998), Lamprell & Whitehead (1992), Wilson (1993), Edgar (1997), Jansen (2000) and Coleman (2003). Higher taxonomic groupings of the Mollusca have been assigned according to the classification outlined in Beesley et al. (1998). Echinoderms were identified according to Edgar (1997) and Shepherd and Thomas (1989).
At the end of each invertebrate survey, algal surveys were undertaken by collecting representative specimens from each morphologically distinct alga.
These samples were transported back to the laboratory and fixed in 10% formalin in seawater for two days, then rinsed and pressed dry between tissue paper.
Identification was based on Edgar (1997), Huisman (2000) and Womersley (1984). In some cases unidentified species were assigned as recognizable
taxonomic units and cross checked between all sites for consistency in their records of occurrence.
Data Presentation & Analysis
Histograms have been prepared to compare mean percent substrate composition across sites by adding the data for each habitat type from the five transects within sites and then dividing by the total cover (*100). The cover of sessile organisms is provided as a mean ( s.e.) per transect. Histograms are also provided for the total species richness of each phyla across sites. Species richness has also been compared for sites inside and outside aquatic reserves, as well as for soft (limestone, aeolinite, calcarenite) and hard (basalt, gneiss, migmatite, schist and granite) using independent t-tests (SPSS version 14). The assumptions of normality were checked by visually by frequency distribution curves and equal variances using the Levenes test in SPSS. Correlation
analyses were performed to test the relationships between 1) species richness of intertidal flora and fauna, 2) the number of habitats and species richness of fauna and flora and 3) complexity and species richness of fauna and flora across all sites. For comparison of species composition across sites, nMDS ordination plots were generated using the PRIMER software package from the Bray-Curtis similarity matrix generated from combined mollusc and echinoderm abundance rankings. Species observed just outside the study sites were included in the species list at that site for these analyses for a more comprehensive of the
communities. Algal data was independently analyzed using presence/absence data.
Results
Overall 9 of the survey sites were characterized as soft (limestone type) reefs and 8 were composed of hard reefs of crystalline igneous, volcanic and metamorphic rocks (Table 1). The number of habitat types observed at the different study sites ranged from five to ten (out of a possible 11, Table 2). The average substrate composition varied greatly between all sites (Figure 2). A substantial amount of horizontal rock platform (exposed and submerged rock, Figure 2a) occurred at all sites except Kings Beach, where the study site occurred within a large boulder field. A large area of submerged and exposed boulders also occurred at Myponga, Carrackalinga, the Bluff and Blanche Point.
Some smaller pebbles occurred at Myponga, Second Valley and Marino Rocks.
Patches of sandy habitat occurred at nine of the sites (Figure 2a). At some sites such as Myponga, sand was recorded under pebbles and boulders (Table 2), but does not appear as sandy substrate in the substrate composition transects (Figure 2a). The mean habitat complexity based on a rugosity index (RI) varied from almost flat (RI = 0.91) at Lady Bay and the Aldinga North site to highly complex (RI = 0.6) at Hallett Cove (Figure 3).
The mean percent cover of sessile organisms ranges from less than 10%
at Marino Rocks, to over 100% at Christies Beach (Figure 2b). Turfing and
foliose algae were the dominant types of sessile organisms occurring across all reefs. Substantial mussel beds were recorded at Port Noarlunga, Christies Beach and Aldinga Reef. Communities of the tube worms occurred in large encrusting beds at seven of the study sites (Figure 2b). Large patches of sea grass habitat were only recorded within the study sites at Blanche Point and Carrackalinga. It should be noted that substantial areas of seagrass habitat also occur in a shallow lagoon in the middle of Aldinga Reef, although not towards the reef edge where the study sites were located.
In total 112 molluscs and 24 echinoderms were recorded across all intertidal reefs along the Fleurieu Peninsula. The total number of algal species tentatively identified in the surveys include 19 Phaeophyta (brown algae), 9 Rhodophyta (red alga) and 18 Chlorophyta (green algae). In addition, 3 species of Magnoliophyta (sea grasses) were recorded. Species lists for each site are provided in Appendix 1. The mean number of molluscan species found on intertidal reefs in the Fleurieu peninsula was 30.3 ( 7.8 st. dev.). The highest molluscan species richness was recorded at Kings Beach (Figure 4a) with more than two standard deviations above the mean (46 species), suggesting this site is a hotspot for molluscan diversity. On the other hand only 12 molluscan species were on the relatively small patches of rocky reef near the Port Noarlunga Jetty.
This site also had no echinoderm species present (Figure 4a) and the lowest species richness of primary producers (Figure 4b). Overall, echinoderms were only recorded at 11/17 sites, with a mean species richness of 1.6 ( 2.3). A
hotspot of echinoderms was recorded at Myponga (Figure 4a) with a total of nine species (>3 standard deviations above the mean). The mean number of primary producers was 12.4 ( 4.4) species. The highest number of algal species was recorded at Hallett Cove (21, Figure 4b), with nearly 2 standard deviations above the mean for all primary producers, despite the absence of any sea grass
(Magnoliophyta). Sea grasses were more common around the Southern tip of the Fleurieu Peninsula (Figure 4b). Within the Port Noarlunga aquatic reserve, both Southport and Port Noarlunga had a noticeable absence of brown algae
(Phaeophyta) and Magnoliophyta. Overall, there was a significant positive correlation between the species richness of the fauna and flora (r2 = 0.284, p = 0.028) surveyed across all reefs in this study (Figure 5).
The species accumulation curves for invertebrate species numbers started leveling off within the last 20min of surveying at most sites (Appendix 2)
suggesting the survey time was generally adequate to accurately represent the species richness. However, reasonable increases in the species richness were recorded in the last 10 minutes at Aldinga, Blanche Point, Hallett Cove and Myponga, suggesting these sites could be somewhat under represented. No further species were recorded after the first 30 minutes of survey at Port Noarlunga (Appendix 2).
On average a high number of species were found on sites outside Aquatic reserves compared to the mean number found at sites inside the Port Noarlunga
and Aldinga Aquatic reserves (Figure 6a). The number of species was
significantly lower inside reserves for both the fauna (molluscs and echinoderms;
d.f. 15; t =2.75, p value = 0.015), but no significant difference was found for the primary producers (d.f. 15; t = 1.91; p = 0.076). All of the reefs inside Aquatic reserves are soft limestone type reefs and the mean number of species on soft rocks was found to be significantly lower than the mean number found on hard rocky reefs (Figure 6b; fauna d.f. 15; t = 3.09 , p value = 0.007; primary
producers d.f. 15; t =2.39; p value = 0.031). There were no significant
correlations between species richness and number of habitats (Figure 7a; fauna r2 = 0.056, p= 0.361; flora r2 = 0.071, p = 0.301) or habitat complexity (Figure 7b fauna r2 = 0.112, p = 0.19; flora r2 = 0.077, p = 0.28) or the percent of cover by sessile organisms (Figure 7c fauna r2 = 0.018, p = 0.611; flora r2 = 0.001, p = 0.924).
nMDS ordination plots from the semi-quantitative abundance rankings for invertebrates revealed broad separation in the community composition from different intertidal reefs along the Fleurieu Peninsula (Figure 8). In particular, the two sites within the Aldinga Aquatic reserve were quite distinct from any other site and two sites within the Port Noarlunga Aquatic reserve also grouped separately from all other sites (Figure 8a). There was also a clear separation in the community composition according to rock type (Figure 8b). ANOSIM revealed a significant difference in invertebrate communities on reefs of different rock type (Global R = 0.299, p value = 0.004). SIMPER analysis revealed 56% dissimilarity
in the communities on hard and soft reefs, with over 70 species contributing to the differences (Appendix 3). Multivariate analyses on the presence/absence of primary producers revealed substantially more overlap between sites (Figure 9a), with no clear separation between hard and soft rocky reefs (Figure 9b). ANOSIM found no significant difference in the algal and plant communities between soft and hard reefs (Global R = -0.009; p value = 0.533).
Discussion
Overall this study revealed great diversity in the physical structure and biological communities occurring on intertidal reefs along the Fleurieu Peninsula.
A relatively high diversity of molluscs, echinoderms and algae on intertidal reefs were found, with records for 185 species in total. The number of species
recorded compare favorably to previous biodiversity assessments along the temperate Australian coastline (e.g. Benkendorff and Davis 2002; Gladstone 2002; Benkendorff 2003, 2005). The number of echinoderm species (24) found was substantially higher than in recent surveys that have been conducted by the same research in S.A. Along the Yorke Peninsula Benkendorff (2005) only recorded 9 echinoderms, whereas on Kangaroo Island Benkendorff et al., (2007) recorded 12 species. But noticeably many of the echinoderms in this study were only recorded at one site, indicating their patchy spatial distribution on South Australian Reefs. The number of molluscan species recorded in the current study also exceeds that found in the previous S.A. studies, but this could be in part related to the higher survey effort i.e. 17 sites were surveyed here compared to
10 on Yorke Peninsula (Benkendorff 2005) and only 5 on Kangaroo Island
(Benkendorff et al., 2007). Nevertheless, more algal species were recorded in the limited surveys on Kangaroo Island (55 species compared to 46 in this study).
A number of species rich hotspots (defined as two standard deviations above the mean across all sites) were recorded in this study. These were found to occur at different sites for molluscs, echinoderms and algae (Figure 4), despite an overall significant correlation in species richness between the invertebrates and flora surveyed (Figure 5). The remote boulder field at Kings Beach supports an unusually large diversity of molluscan species, whereas the complex boulder field at Myponga was a hotspot for echinoderms. This reef at Myponga also supported a higher diversity of molluscs and should be considered a priority for conservation based on the presence of a large number of brittle stars which occurred at no other site (Appendix 1). Since these fragile organisms live under boulders, it is possible that the high level of recreational use prevents their
persistence at some other apparently suitable sites. Hallett Cove was found to be a hotspot for algal diversity (Figure 4b), which was surprising given the relatively low percent cover of sessile organisms, including algae (Figure 2b). The large reef at Aldinga and several other sites around the tip of Fleurieu Peninsula appear to support a good mix of algae and seagrass (Figure 4b).
As a consequence of the limited species inventory data, the application of systematic reserve selection procedures is typically very limited in the marine
environment (Pressey and McNeill 1996; Gladstone 2002). Along the Fleurieu Peninsula, two Aquatic reserves have been designated: Aldinga Reef and Port Noarlunga Aquatic reserves (PIRSA Fisheries 2007). In terms of biodiversity conservation, the current aquatic reserves along the Fleurieu Peninsula do not appear to be protecting particularly high numbers of species. In fact, comparison of the mean number of species occurring on reefs inside and outside aquatic reserves revealed significantly lower numbers of species in the reserves for both the invertebrates and flora (Figure 6a). This may be in part influenced by the fact that sites within the reserves are all soft limestone type reefs, whereas a higher diversity of species was recorded on the harder rocky reefs surveyed in this study (Figure 6b). Nevertheless, Williams (1996) also reported a significantly higher diversity and taxa richness on similar limestone reefs outside these two reserves compared to locations within the Aquatic reserves.
Aldinga Reef is designated as a biodiversity reserve to protect aquatic plants and animals associated with the very tertiary limestone platform (PIRSA Fisheries 2007). The size of this reef makes it difficult to adequately represent in our 20 x 20m plots used for rapid biodiversity assessment. Nevertheless, it is surprising that the two survey sites at on this reef did not record a particularly high number of molluscan species. Unusually high densities of the predatory crab Ozius truncatus were observed at this site and previous studies by Chilton & Bull (1984, 1986) have shown that Ozius can affect the size distribution of gastropods at Aldinga reef. This, in addition to high recreational activity, such as reef walking
(Wiliams 1996) and overturning boulders may be influence the diversity of species on this aquatic reserve.
The Port Noarlunga aquatic reserve is designated for the protection of reef organisms from exploitation and encompasses intertidal reefs near the Jetty, at Christies Beach and on the edge of Onkaparinga Head (South Port). The rocky reefs at Port Noarlunga beside the jetty were highly diminished in all taxa compared to the other locations. This is likely to be due to high recreational activity (Williams 1996). There was also a noticeable amount of pollution from recreational boating fuel and oil in the water at the time of this survey, which could have negative impacts on the local marine organisms (e.g. Piller, 1998).
Some very common gastropods such as Nerita atramentosa, Austrocochlea spp.
and Bembicium nanum were absent or rare within the Port Noarlunga Aquatic reserve sites, but present at all other locations along the coast (Appendix 1).
In terms of ensuring an adequate representation of intertidal reefs in Marine Parks with in the Fleurieu Peninsula Bioregions, it will be necessary to expand the current reserve system. In particular, hard reefs comprised of
igneous and metamorphic rock should be represented to compliment the current limestone reefs, as these were found to support distinct ecological communities for the invertebrate taxa surveyed (Figure 8). The proposed Encounter Marine Park (S.A. DEH Coast and Marine, 2007) should help facilitate a more
comprehensive representation of a range of different intertidal substrates and
habitats (see Tables 1 & 2). Further survey work, including species inventories will need to be undertaken in other S.A. bioregions. Based on this data from the Fleurieu Peninsula, it appears that habitat data, such as number of habitats, habitat complexity and percent of cover by sessile organisms can not be used as a surrogate for intertidal biodiversity assessment (Figure 7).
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Table 1: The location of 17 study sites, dates surveyed, tidal and weather conditions for intertidal surveys along the
Fleurieu Peninsula, S.A. The orientation of the reef is provided for the principle direction looking out to sea. Rock type is classified as soft for limestone, calcaranite and aeolinite reefs, whereas hard reefs were composed of basalt, gneiss, migmatite, schist or granite.
Site Latitude Longitude Date
surveyed
Tidal
height Weather Orientation
Rock type
Marino S35.04445 E138.50838 23.11.06 0.2 sunny W hard Hallett Cove S35.07425 E138.49518 3.1.07 0.27 sunny W hard
Christies Beach S38.08587 E138.28017 2.3.07 0.27 sunny W soft Port Noarlunga S35.08925 E138.28015 2.3.07 0.27 sunny W soft
South Port S35.16528 E138.46773 5.1.07 0.24 light rain W soft Blanche Point S 35.24669 E138.46127 24.11.06 0.27 sunny NW soft
Aldinga North S35.26863 E138.44135 21.12.06 0.15 cloudy W soft Aldinga South S35.2750 E138.43979 20.12.06 0.19 cloudy W soft
Myponga S35.37132 E138.38272 9.1.07 0.25 sunny NE hard Carrackalinga S35.41961 E138.32304 6.1.07 0.24 cloudy NW soft Lady Bay S35.47256 E138.28733 22.12.06 0.15 light rain W soft
Second Valley S35.51084 E138.21484 4.1.07 0.25 sunny SWW hard Fishery Beach S35.63328 E138.11530 24.1.06 0.29 windy SW hard Kings Beach S35.60323 E138.58235 24.1.06 0.25 sunny NEE hard The Bluff S35.58624 E138.59976 22.12.06 0.15 windy NE hard
Yilki S35.57985 E138.59818 20.12.06 0.19 breeze SEE soft Middleton S35.51635 E138.70493 17.1.07 0.25 windy SE hard
Table 2: The present of different habitats observed within the 17 intertidal study sites along the Fleurieu Peninsula, S.A.
Boulder fields and sand are only recorded as present if there was a patch of more than 2m2 within the study site.
Site
Bare Rock
Boulder
Field Sand Crevices
Rock Pools
Supra littoral
Mussel Beds
Foliose Algae
Turfing Algae
Sea grass
Galeolaria Crust
Total habitats Marino y n y y y y y y n n y 8 Hallett Cove y y y y y y y y y n y 10 Christies Beach y n y y y n y y y n n 7 Port Noarlunga y n y n n n y y y n n 5 South Port y n y y y n y y y n y 8 Blanche Point y y y y y n y y y y n 9 Aldinga North y n n y y n y y y n n 6 Aldinga South y y y n y n y y y y n 8 Myponga y y y y y n n y y n n 7 Carrackalinga y y n y y y y y y y y 10 Lady Bay y y y y y n y y y y n 9 Second Valley y y n y y y y y y n y 9 Fishery Beach y y n y y y n y y n y 8 Kings Beach y y n y y n n y y n y 7 The Bluff y y y n y y n y n n n 6 Yilki y y y y y n n y y n y 8 Middleton y n n y y y y y y n y 8
Figure 1: The location of 17 study sites sampled for intertidal reef habitat and biodiversity along the Fleurieu Peninsula, S.A.
0 10 20 30 40 50 60 70 80 90 100
Marino Rocks Hallett Co
ve
Christies Beach Port Noar
lunga Southport
Blanche P oin
t
Aldin ga Re
ef N
Aldinga Reef S My
ponga Be ach Carrickalinga
Lady B ay
Second Valley Fis
heries Beac h
Kings B eac
h The B
luff Yilki Beach
Middleto n
Percent cover
Exposed Pebbles Submerged Pebbles Exposed Sand Submerged Sand
Submerged Loose Boulders Exposed Loose Boulders Submerged Rock Exposed Rock
0 20 40 60 80 100 120 140
Marino Rocks Hallett Co
ve
Ch
risties Beach Port Noarlunga
Sout hpor
t
Blanch e P
oint
Aldinga Re
ef N
Aldinga Re
ef S
Mypon ga Beach
Carrickalinga Lady Bay
Sec ond Val
ley
Fishe ries Beach
Kings Beach
The Bluff
Yilki Beach Middleton
Mean Percent Cover + s.e.
Mixed Mussel/Algae Community
Galeolaria Crust Seagrass Turfing Algae Foliose Algae
Figure 2: Mean percent cover of substrate for a) abiotic habitat and b) sessile organisms at 17 intertidal reefs along the Fleurieu Peninsula, S.A.
a)
b)
0.00 0.10 0.20 0.30 0.40 0.50 0.60 0.70 0.80 0.90 1.00
Marino Rock s Hallet Cove
Christies B eack Port N
oar lunga
Sout h P
ort Blanc
he P t
Aldinga N orth Aldinga S
outh Myponga
Carrackalinga Lady
Bay Second V
alley Fisher
y B eac
h Kings
Beac h The
Bluff Yilki
Middleton
Habitat rugosity index
Figure 3: Habitat complexity at 17 intertidal rocky reef sites along the Fleurieu Peninsula, S.A Complexity is based on a rugosity index whereby values closer to one are more flat and those closer to zero are highly complex.
0 5 10 15 20 25
Marino Rocks
Halle tt C
ove
Christies Beac
h
Port Noarlunga Southport
Blanc he Point
Aldinga North Aldinga
South Myponga Beach
Carrickaling a Lady B
ay
Second V alley
Fis heries B
eac h
Kings B each
The B luff Yilki Be
ach Middleton
Species richness
Magnoliophyta Rhodophyta Chlorophyta Phaeophyta 0
10 20 30 40 50 60
Marino Hallet
Cove Christies B
each Pt No
arlunga South Port
Blanche Aldi
nga N th Aldinga S
th Myponga
Carrac kaling
a Lady B
ay
Seco nd V
alley Fishery B
each Kings B
eac h
The B luff
Lady B ay
Middleton
North > South
Species richness
Echinoderms Molluscs
Figure 4: The number of species of a) molluscs and echinoderms and b) primary a)
b)
y = 0.265x + 3.9355 R2 = 0.2839
0 5 10 15 20 25
0 10 20 30 40 50 60
Fauna species richness
Flora species richness
Figure 5: Correlation between the number of fauna (molluscs and
echinoderms) and the number of flora (algae and seagrasses) found on 17 intertidal reefs along the Fleurieu Peninsula, S.A.
0 5 10 15 20 25 30 35 40
Outside reserves Inside reserves
Mean Species richness
invertebrates primary producers
0 5 10 15 20 25 30 35 40 45
Hard Rock Soft Rock
Mean Species Richness
invertebrates primary producers
Figure 6: The mean number of invertebrates (molluscs and echinoderms) and primary producers (algae, seagrass and lichen) found on rocky reef along the Fleurieu Peninsula S.A. grouped according to a) Aquatic reserve status and b) rock type. Error bars represent standard error of the mean.
a)
b)
0 10 20 30 40 50 60
0 2 4 6 8 10 12
Number of habitats
Fauna species richness
0 5 10 15 20 25
0 2 4 6 8 10 12
Number of habitats
Flora species richness
0 10 20 30 40 50 60
0.00 0.20 0.40 0.60 0.80 1.00
Habitat rugosity
Fauna species richness
0 5 10 15 20 25
0.00 0.20 0.40 0.60 0.80 1.00
habitat rugosity
Flora species richness
0 10 20 30 40 50 60
0.00 20.00 40.00 60.00 80.00 100.00 120.00 Total cover of sessile organisms
Fauna species richness
0 5 10 15 20 25
0.00 20.00 40.00 60.00 80.00 100.00 120.00 Total cover of sessile organisms
Flora species richness
Figure 7: The relationship between species richness and a) number of intertidal habitats, b) habitat rugosity and c) cover of sessile organisms at 17 intertidal reefs. Left panels represent species richness of fauna (molluscs and echinoderms), whereas right panels represent species a)
c) b)
soft
hard Stress: 0.17
Pt Noarlunga Christies Beach
Marino
Blanche
Aldinga South Yilki Beach
Aldinga North
Lady Bay The Bluff
Hallet Cove Second Valley
South Port Carrackalinga Myponga
Middleton Kings Beach
Fishery Beach
Stress: 0.17
Figure 8: nMDS ordinations for mollusc and echinoderm community composition showing the differences between a) 17 sites and b) sites grouped according to rock type.
a)
b)
Marino Rocks
Hallet Cove Christies Beach
Port Noarlunga Southport
Blanche Point Aldinga north
Aldinga south
Myponga Beach
Carrickalinga Lady Bay
Second Valley Fisheries Beach
Kings Beach The Bluff Yilki Beach
Middleton
Stress: 0.19
Hard
Soft Stress: 0.19
Figure 9: nMDS ordinations for algal and plant community composition showing the differences between a) 17 sites and b) sites grouped according to rock type.
a)
b)
Appendix 1
Appendix 1: Species occurrence for a) macromolluscs, b) echinoderms and c) marine flora recorded on 17 intertidal reefs in South Australia; MR = Mario Rocks, HC = Hallett Cove, CB = Christies Beach , PN = Port Noarlunga, SP = South Port, BP = Blanche Point, AN = Aldinga North, AS= Aldinga South, My = Myponga, Ca = Carrackalinga, LB = Lady Bay, SV = Second Valley, FB = Fishery Beach, KB = Kings Beach, TB = The Bluff, YB = Yilki Beach, Mi = Middleton. Semi-quantitative abundance ranking are used for the invertebrates, whereby R = rare < 5 individuals; U = Uncommon 6-20 individuals; C = Common 21-100 individuals; A = Abundant >100 individuals. For the marine plants 1 = present and 0 = absent. Extra notes are made in the mollusc table for the presence of egg masses (egg) and shells (She), as well as records where species were recorded outside the 20x 20 m plot on the same reef (out).
a) MOLLUSCA
Class/ Subclass
Family Species MR HC CB PN SP BP AN AS My Ca LB SV FB KB TB YB Mi Eogastropoda
Patellidae Patella peronii 0 U 0 0 0 R R 0 R 0 0 0 R C 0 0 0 Nacellidae Cellana tramoserica C A R 0 U C 0 0 C U A A C U 0 0 U
Cellana solida A A C 0 C C 0 0 C C R A A A C R C
Lottidae Collisella mixta 0 U 0 0 U 0 0 0 R 0 0 U 0 0 0 0 R
Notoacmea mayi 0 C 0 0 C U 0 0 0 0 0 C 0 U 0 R C
Notoacmea petterdi A A U A A A U C A C A C A C C C A
Notoacmea flammea 0 R 0 0 0 R A 0 0 0 0 C C 0 C 0 0
Patelloida cf. insignia 0 R 0 0 R 0 C 0 C 0 0 U 0 U 0 0 0
Patelloida alticostata R U R 0 0 R U 0 U U 0 C C A 0 0 U
Patelloida profunda calamus C 0 0 0 U 0 0 0 0 R C U C C 0 R R
Patelloida latistrigata A U 0 0 0 0 U 0 C C C A 0 C 0 0 A
Neritopsidae Nerita atramentosa
A A
0 0
0 out 0 out A + egg
A +
egg A A +
egg A C C 0 U Orthogastropoda
Haliotidae Haliotis rubra 0 R R 0 0 U R 0 R 0 0 0 0 R 0 0 0
Haliotis laevigata 0 0 0 0 0 U 0 0 0 0 0 0 0 0 0 0 0
Haliotis sp. 0 0 0 0 0 0 0 0 R 0 0 0 0 0 0 0 0
Fisurellidae Clypidina rugosa R 0 0 0 R 0 U R R 0 C 0 U 0 R U 0
Amblychilepas javanicensis 0 0 0 0 0 0 0 0 0 0 0 0 0 R 0 0 C
Cosmetalepas cancatenatus R 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0
Scutus antipodes 0 0 0 0 0 0 0 0 0 0 0 0 0 0 R 0 0
Trochidae Austrocochlea concamerata 0 0 0 0 U 0 0 out A U U C C U A 0 C
Austrocochlea odontis 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 she 0
Austrocochlea adelaidae R C 0 0 R 0 0 0 0 0 0 0 U A 0 0 A
Austrocochlea porcata 0 C 0 0 A 0 0 0 0 A 0 A A U A 0 0
Austrochoclea constricta U out 0 0 A out 0 0 0 C U A C C A A A
Notogibbula preissiana R U 0 0 0 0 R 0 U 0 R R R C 0 0 0
Clanculus consobrinus 0 0 0 0 0 0 0 0 0 0 0 R 0 C 0 R C
Clanculus cf limbatus 0 0 0 0 0 0 0 0 0 0 0 0 0 U 0 U 0
Clanculus c.f. undatum 0 0 0 0 0 0 0 0 0 0 0 0 0 U 0 0 0
Granata imbricata 0 0 0 0 0 0 0 0 U R 0 0 0 0 U U 0
Euchelus profunior R 0 0 0 0 R 0 U C 0 0 R 0 0 0 0 R
Canthrindella picturata 0 U 0 R U 0 0 U U 0 R U 0 U R 0 0
Herpetoma pumilo 0 R 0 0 0 0 U 0 0 R 0 R 0 R R U 0
Thalotia chlorostoma 0 U out 0 0 0 R 0 0 0 0 0 R R 0 R 0
Thalotia conica R 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0
Cantharidus (Thalotia)
pullcherrimus 0 0
0 U
0 0 R 0 0 0 0 R 0 0 0 0 0
Cantharidus (Thalotia)
lehmanni 0
0 0 0 0 0 0 0 0 0 0 0
0 0
0 0 R
Phasianotrochus juvenlies? 0 0 U 0 0 0 0 0 0 0 0 0 0 0 0 0 0
Minolia cf cincta 0 0 0 0 0 0 0 0 0 0 0 0 0 C 0 0 0
Astele (Calliostoma) monile 0 0 0 0 0 0 R 0 0 0 0 0 0 0 0 0 0
unid black ridged 0 0 0 0 0 0 0 0 0 R 0 0 0 0 0 0 0 Unidentified juveniles R 0 0 0 C 0 0 0 0 0 0 U 0 0 0 0 0 Turbinidae Turbo undulatus U C C C A 0 C 0 0 0 U C A C 0 C U
Austroliotia australis 0 0 0 0 0 0 0 0 R 0 0 0 0 0 0 0 0
Australium cf squamiferum 0 0 0 0 0 0 out 0 0 0 0 0 0 0 0 0 0
Phasianella australis 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 R
Phasianella ventricosa 0 0 U R 0 0 0 0 0 0 0 0 0 U 0 0 0
Cererthidae Bittium granarium 0 0 0 0 0 C C U A U U 0 0 C U C R
Bittium c.f. icarus 0 0 0 0 0 0 0 0 C 0 R 0 0 0 0 0 0
unidentified 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 U 0
Batillariidae Zeacumantus diemenensis 0 0 0 0 0 0 0 0 0 0 0 0 0 0 A R 0
Batllaria estuarina 0 0 0 0 0 0 C R 0 0 0 0 0 0 0 0 0
Littorinidae Bembicium nanum A C R 0 A out 0 out U R C C C U 0 0 A
Littorina acutispira C C 0 out 0 0 0 0 out C 0 0 A C 0 0 A
Littorina unifasciata A A 0 out 0 U 0 0 out A 0 A A A A 0 A
Nodilittorina praetermissa C C 0 0 0 0 0 0 0 0 C 0 0 U 0 C
Rissoina crassa 0 0 U U 0 C C R 0 R 0 U R 0 0 0 0
Rissoina sp. 0 0 0 0 0 0 0 0 C 0 0 0 0 0 R 0 0
Cypraea Cypraea compti 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 Hipponicidae Hipponix australis 0 0 0 0 0 0 R 0 0 0 0 0 0 0 0 R 0 Naticidae Sinum scf zonale 0 0 0 0 0 0 0 0 R 0 0 0 0 0 0 0 0 Calyptraeidae Crepidula aculeata 0 0 0 0 0 0 0 0 0 0 R 0 0 0 0 0 0 Buccinidae Cominella lineolata 0 0 0 0 0 0 0 she 0 C she 0 R U R U 0
Cominella eburnea 0 0 0 0 0 0 0 she 0 0 she 0 0 0 R 0 0
Naticidae Polinices sp.
0 0
0 0
0 0 0 0 0 0 0 0 0 0 0 R
egg she Columbellidae Mitrella pulla 0 0 0 0 0 0 R 0 R 0 0 0 0 0 R 0 R Muricidae Lepsiella vinosa 0 0 0 0 0 0 0 0 U 0 C C C 0 0 U U
Dicathais orbita C C 0 0 0 U out 0 R 0 R C U U 0 R C
Lepsiella flindersii
0 0
0 0
0 0 0 0 0 0 she C 0 R +
egg C 0 0
Lepsiella reticulata 0 0 0 0 0 0 0 0 0 0 0 0 0 R 0 0 0
Nassaridae Nassarius pyrrhus 0 0 0 0 0 0 0 0 0 0 she 0 0 0 0 0 0 Conidae Conus anemone
0 0
0 0
0 0 0 0 0 0 she 0 0 0 R R +
egg 0 Epitoniidae Epitonium sp 0 0 0 0 R 0 0 0 0 0 0 0 0 0 0 0 0 Siphonariidae Siphonaria zelandica
0 0
A A
out 0 U C A U A U C A C +
egg A U
Siphonaria diemenensis
A A
A A
A A C A A A A A A A A +
egg A U
Siphonaria sp. C A C 0 A C 0 0 U C A A A A U A A
Tylodinidae Tylodina sp. 0 0 0 0 0 0 R 0 0 0 0 0 0 0 0 0 0 Dorididae Discodoris sp. 0 0 0 0 0 0 0 R 0 0 0 0 0 0 0 0 0
Rostanga c.f. calumus
0 0
0 0
0 0 0 0 0 0 0 0 0 R +
egg 0 0 0
Hoplodoris nodulosa 0 0 R 0 0 0 0 0 0 0 0 0 0 0 0 0 0
Dendodorididae Doriopsilla sp.
0 0
0 0
0 0 0 0 0 0 U +
egg 0 0 0 0 0 0 Chromodoridae Verconia verconis 0 out 0 0 0 R 0 0 0 0 0 0 0 0 0 0 0
Dendrodoris nigra
0 0
0 0
0 0 0 0 0 0 0 0 0 0 0 R + egg 0
Hypselodoris obscura
0 0
R 0
0 R 0 R +
egg 0 0 0 0 0 0 0 0 0
Chromodoris sp. 0 0 R 0 0 0 0 0 0 0 0 0 0 0 0 0 0
Facelinidae Austraeolis ornata 0 R 0 0 0 0 0 R 0 0 0 0 0 0 R 0 0 Madrellidae Mandrella sanguinea 0 R 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 unidentified egg ribbons 0 0 0 0 0 0 R 0 0 0 0 0 0 0 0 0 0 Polyplacophora
Ischnochitonidae Ischnochiton elongatus R C U R R C U U C U A U C C A C A
Ischnochiton virgatus 0 0 0 0 0 0 0 0 0 0 0 U 0 0 U U U
Ischnochiton australis 0 C 0 0 0 U 0 0 R 0 0 U 0 C C 0 A
Ischnochiton lineolatus 0 0 0 0 0 0 0 0 U 0 U R 0 R R 0 0
Ischnochiton tori 0 0 0 0 0 R R 0 R R 0 R 0 0 U 0 U
Ischnochiton cariosus R 0 R 0 0 0 U 0 0 R 0 0 0 0 0 U 0
Ischnochiton smaragdinus R R R 0 0 R 0 0 R 0 0 R 0 0 0 0 R
Ischnochiton resplendens 0 0 0 0 0 0 R 0 U 0 R 0 0 R 0 0 0
Ischnochiton variegatus 0 0 0 0 R 0 0 0 0 0 R 0 0 0 U 0 0
Acanthochitonidae Acanthochiton sp. 0 0 0 0 0 R 0 0 0 0 0 0 0 R 0 0 0 Mopalidae Plaxiphora albida 0 U 0 0 0 0 0 0 0 0 0 0 0 R 0 0 R Bivalvia
Galeommatidae Lasea australis R R U 0 C R R U R U 0 0 0 0 R 0 U Solemyidae Barbatia sp. 0 0 0 0 0 0 R U 0 0 R 0 0 R R U 0 Mytilidae Brachidontes erosa 0 0 0 0 C R U U 0 0 R 0 0 0 0 U 0
Xenostrobus pulex A A A A A A A C out A A A 0 U 0 U A
Mytilus sp. 0 0 R 0 0 0 0 0 0 0 0 0 0 0 0 0 0
Trichomya hirsuta 0 0 0 R 0 0 0 R 0 0 R 0 0 0 0 0 0
Musculus sp. 0 U 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0
Ostreidae Ostrea angasi 0 U R 0 C U U C 0 C 0 U 0 0 0 0 0
Saccostrea glomerata 0 U U 0 0 0 0 0 0 0 0 0 0 0 0
Pteriidae Pinctada sp. 0 0 0 0 0 0 0 R 0 0 0 0 0 0 0 0 0 Malleidae Malleus c.f. meridianis 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 Veneridae Katelysia peronii 0 0 0 0 0 0 0 0 0 0 R 0 0 0 0 0 0 Lucinidae Codakia rugifera 0 0 0 0 R 0 0 0 0 0 0 0 0 0 0 0 0 Cephalopoda
Decapoda Sepioteuthis australis
R +
egg 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 Total 26 34 24 12 27 28 32 20 36 28 30 40 27 46 34 31 37
