Victorian Subtidal Reef Monitoring Program - Parks Victoria

PARKS VICTORIA TECHNICAL SERIES NUMBER 25

Victorian Subtidal Reef Monitoring Program The Reef Biota on the Western Victorian Coast Volume 2 Authors: Simon P Hart, Matt Edmunds, John Elias, Chelsea Ingwersen March 2005

© Parks Victoria

All rights reserved. This document is subject to the Copyright Act 1968, no part of this publication may be reproduced, stored in a retrieval system, or transmitted in any form, or by any means, electronic, mechanical, photocopying or otherwise without the prior permission of the publisher.

First published 2005 Published by Parks Victoria Level 10, 535 Bourke Street, Melbourne Victoria 3000

Opinions expressed by the Authors of this publication are not necessarily those of Parks Victoria, unless expressly stated. Parks Victoria and all persons involved in the preparation and distribution of this publication do not accept any responsibility for the accuracy of any of the opinions or information contained in the publication.

Authors: Simon P Hart Matt Edmunds John Elias Chelsea Ingwersen

National Library of Australia Cataloguing-in-publication data Includes bibliography. ISSN 1448-4935

Citation Hart, S.P., Edmunds, M., Elias, J. and Ingwersen, C. (2005) Victorian Subtidal Reef Monitoring Program: The Reef Biota on the Western Victorian Coast. Volume 2. Parks Victoria Technical Series No. 25. Parks Victoria, Melbourne.

Printed on environmentally friendly paper

Parks Victoria Technical Series No. 25

West Coast Subtidal Reef Monitoring


Victorian Subtidal Reef Monitoring Program: The Reef Biota on the Western Victorian Coast. Volume 2.

Simon P Hart, Matt Edmunds John Elias, Chelsea Ingwersen

Australian Marine Ecology Pty Ltd

March 2005

III



EXECUTIVE SUMMARY Shallow reef habitats cover extensive areas along the Victorian coast and are dominated by seaweeds, mobile invertebrates and fishes. These reefs are known for their high biological complexity, species diversity and productivity. They also have significant economic value through commercial and recreational fishing, diving and other tourism activities. In order to effectively manage and conserve these important and biologically rich habitats, the Victorian Government has established a long-term Subtidal Reef Monitoring Program (SRMP). Over time the SRMP will provide information on the status of Victorian reef flora and fauna and determine the nature and magnitude of trends in species populations and species diversity through time. Monitoring occurred at locations in two different marine bioregions. In the Central Victorian Bioregion, survey sites were established in the Point Addis Marine National Park and the Eagle Rock and Marengo Reefs Marine Sanctuaries. In the Otway Bioregion, survey sites were established at Merri Marine Sanctuary. In total, ten monitoring sites have been established. There are two sites within the Point Addis Marine National Park and one site within each of the Marine Sanctuaries. There is an equivalent number of reference sites outside of each of the marine protected areas. Subtidal reef monitoring uses standardised underwater visual census methods to survey algae, macroinvertebrates and fish. Surveys occur in shallow water between 3 and 8 m deep. This report aims to: provide general descriptions of the biological communities and species populations at each monitoring site in December 2003-January 2004; identify any unusual biological phenomena such as interesting or unique communities or species; and identify any introduced species at the monitoring locations. The surveys were done along a 200 m transect line. Each transect was surveyed for: 1. abundance and size structure of large fishes; 2. abundance of cryptic fishes and benthic invertebrates; 3. percentage cover of macroalgae; and 4. density of dominant kelp species.

IV



To date over 150 different species have been observed during the monitoring program in and around the marine protected areas along the western Victorian coast. At most sites, algal assemblages were dominated by a canopy of large brown algal species including Phyllospora comosa and Ecklonia radiata along with the smaller brown algae Seirococcus axillaris and Acrocarpia paniculata. Understorey assemblages were typical of other exposed southern Victorian locations and consisted largely of various species of fleshy and corraline red algae. The Point Addis and Merri sites had similar algal community structure, whereas the Eagle Rock and Marengo sites showed less clear patterns between paired marine sanctuary and reference sites. Invertebrate species richness and diversity was relatively even across all monitoring sites. Species diversity was lower where blacklip abalone Haliotis rubra and warrener Turbo undulatus were the numerically dominant species. There were substantial differences in invertebrate assemblage structure between all sites. However, there were some similarities between sites within and outside each marine protected area. Species common to all or most sites were blacklip abalone H. rubra, warrener T. undulatus, the dog whelk Dicathais orbita, and the featherstar Cenolia trichoptera. Echinoderm assemblages varied between the sites; Nectria macrobrachia was a relatively common species. Fish species richness varied between 9 and 17 species but was between 12 and 14 species for most sites. Fish species diversity was relatively even across all sites. There were few clear patterns in fish assemblage structure although some similarities between paired MS/MNP sites and reference sites were apparent. Blue-throat wrasse Notolabrus tetricus occurred at all sites and was often the most abundant fish. Other fish species common to all or most sites were herring cale Odax cyanomelas and scalyfin Parma victoriae. Common leatherjackets were yellow tailed Meuschenia flavolineata and horseshoe M. hippocrepis. Results from the one monitoring survey allow us to describe reef community structure for a single short snapshot in time. Reef communities are dynamic over short, medium and long time scales. As monitoring continues and longer-term datasets are accumulated (over multiple years to decades) the program will be able to more adequately reflect trends and changes in community or population structure as well as to identify specific ecological patterns occurring in these ecosystems.

V



CONTENTS EXECUTIVE SUMMARY........................................................................................... IV CONTENTS............................................................................................................... VI Figures............................................................................................................................................... vii Tables............................................................................................................................................... viii

1.0 INTRODUCTION .................................................................................................. 1 1.1 Subtidal Reef Ecosystems on the Victorian Coast.......................................................................1 1.2 Subtidal Reef Monitoring Program ...............................................................................................6

2.0 METHODS............................................................................................................ 9 2.1 Site Selection and Survey Times .................................................................................................9 2.2 Census Method ..........................................................................................................................14 2.3 Data Analysis .............................................................................................................................17

3.0 MACROALGAE ................................................................................................ 21 3.1 Species Richness and Diversity.................................................................................................21 3.2 Community Structure..................................................................................................................22 3.3 String Kelp Macrocystis Angustifolia ...........................................................................................27

4.0 INVERTEBRATES AND CRYPTIC FISHES ..................................................... 29 4.1 Species Richness and Diversity.................................................................................................29 4.2 Assemblage Structure ................................................................................................................29 4.3 Population Abundances and Sizes ............................................................................................33

5.0 FISH .................................................................................................................. 35 5.1 Species Richness and Diversity.................................................................................................35 5.2 Community Structure...................................................................................................................35 5.3 Population Structure....................................................................................................................39

6.0 REFERENCES .................................................................................................. 41 7.0 ACKNOWLEDGEMENTS ................................................................................. 43

vi



INDEX OF FIGURES AND TABLES Figures Figure 1.1 Examples of macroalgae found on subtidal reefs on the Victorian coast. ............................ 2 Figure 1.2 Examples of species of invertebrates and cryptic fish found on Victorian subtidal reefs...... 5 Figure 1.3 Examples of fish species found on Victorian subtidal reefs .................................................. 5 Figure 1.4 An example plot depicting change in an environmental, population or community variable over time (days, months or years). The black circles denote examples of monitoring times. Note how data from these times may not necessarily reflect patterns over shorter time periods, or true maxima or minima over longer time periods. Note further how data from any window of 2 or 3 consecutive monitoring times fails to adequately estimate the patterns or variation over the longer time period. ..... 7 Figure 2.1 Location of monitoring sites inside and outside the Point Addis Marine National Park. The park boundary is shown in blue and the monitoring sites are shown in red.......................................... 10 Figure 2.2 Location of monitoring sites inside and outside the Eagle Rock Marine Sanctuary. The park boundary is shown in blue and the monitoring sites are shown in red.................................................. 11 Figure 2.3 Location of monitoring sites inside and outside the Marengo Reefs Marine Sanctuary. The park boundary is shown in blue and the monitoring sites are shown in red.......................................... 12 Figure 2.4 Location of monitoring sites inside and outside the Merri Marine Sanctuary. The park boundary is shown in blue and the monitoring sites are shown in red.................................................. 13 Figure 2.5 Biologist-diver with transect reel, Lonsdale Back Beach. ................................................... 20 Figure 2.6 The cover of macrophytes is measured by the number of points intersecting each species on the quadrat grid. ............................................................................................................................... 20 Figure 3.1 MDS plot of algal assemblage structure on the west coast of Victoria December 2003January 2004. The numbers on each plot denote the survey site. Kruskall stress = 0.08.................... 23 Figure 3.2 Toothbrush leatherjacket Acanthaluteres vittiger swimming between Macrocystis angustifolia plants.................................................................................................................................. 28 Figure 4.1 MDS plot of invertebrate assemblage structure on the west coast of Victoria, December 2003-January 2004. The labels next to each point denote the survey site. Kruskall stress = 0.12 ...... 30 Figure 4.2 Abundance of common invertebrates on subtidal reefs on the west coast of Victoria........ 33 Figure 4.3 Size frequency distributions for Haliotis rubra at monitoring sites on the west coast of Victoria................................................................................................................................................... 34 Figure 5.1 MDS plot of fish assemblage structure on the west coast of Victoria, December 2003January 2004. The labels next to each point denote the survey site. Kruskall stress = 0.13 ............... 37

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Tables Table 2.1 Subtidal reef monitoring sites on the west coast of Victoria ................................................. 14 Table 2.2 Survey times for subtidal reef monitoring on the western coast of Victoria. ......................... 14 Table 2.3 Mobile fishes, including sharks and rays, surveyed using Method 1 and macroinvertebrates and cryptic fishes surveyed using Method 2 on the western coast of Victoria...................................... 16 Table 2.4 Macroalgae (Method 3) surveyed on the western coast of Victoria...................................... 17 Table 3.1 Diversity statistics for algae on the western coast of Victoria during the first survey: pooled values for number of species, heterogeneity and species evenness for each site. .............................. 22 Table 3.2 Macroalgal abundance (percent cover) at each monitoring site on the western coast of Victoria. Surveys occurred between December 2003-January 2004.................................................... 25 Table 3.2 (continued) Macroalgal abundance (percent cover) at each monitoring site on the western coast of Victoria. Surveys occurred between December 2003-January 2004. ..................................... 26 Table 3.2 (continued) Macroalgal abundance (percent cover) at each monitoring site on the western coast of Victoria. Surveys occurred between December 2003-January 2004. ..................................... 27 Table 4.1 Species richness and diversity of invertebrates on the west coast of Victoria .................... 29 Table 4.2 Abundance of megafaunal invertebrates and cryptic fishes (200 m-2) at sites on the west coast of Victoria, December 2003-January 2004. ................................................................................. 32 Table 5.1 Fish species richness and diversity on the west coast of Victoria. ....................................... 35 Table 5.2 Fish abundance (2000 m-2) at monitoring sites on the west coast of Victoria, December 2003-January 2004................................................................................................................................ 38 Table 5.3 Population structure of blue throated wrasse Notolabrus tetricus on the west coast of Victoria................................................................................................................................................... 39 Table 5.4 Population structure of purple wrasse Notolabrus fucicola on the west coast of Victoria .... 40 Table 5.5 Population structure of herring cale Odax cyanomelas on the west coast of Victoria.......... 40

viii



1.0 INTRODUCTION 1.1 Subtidal Reef Ecosystems on the Victorian Coast Shallow reef habitats cover extensive areas along the Victorian coast. The majority of reefs in this area are exposed to strong winds, currents and large swell. A prominent biological component of Victorian shallow reefs are kelp and other seaweeds (Figure 1.1). Large species, such as the common kelp Ecklonia radiata and crayweed Phyllospora comosa, are usually present along the open coast in dense stands. The production rates of dense seaweed beds are equivalent to the most productive habitats in the world, including grasslands and seagrass beds, with approximately 2 kg of plant material produced per square metre per year. These stands typically have 10-30 kg of plant material per square metre. The biomass of seaweeds is substantially greater where giant species such as string kelp Macrocystis angustifolia and bull kelp Durvillaea potatorum occur. Seaweeds provide important habitat structure for other organisms on the reef. This habitat structure varies considerably, depending on the type of seaweed species present. Tall vertical structures in the water column are formed by Macrocystis angustifolia, which sometimes forms a dense layer of fronds floating on the water surface. Other species with large, stalk-like stipes, such as Ecklonia radiata, Phyllospora comosa and Durvillaea potatorum, form a canopy 0.5-2 m above the rocky substratum. Lower layers of structure are formed by: foliose macroalgae typically 10-30 cm high, such as the green Caulerpa and red Plocamium species; turfs (to 10 cm high) of red algae species, such as Pterocladia capillacea; and hard encrusting layers of pink coralline algae. The nature and composition of these structural layers varies considerably within and between reefs, depending on the biogeographical region, depth, exposure to swell and waves, currents, temperature range, water clarity and presence of sand.

1



Crayweed Phyllospora comosa canopy

Common kelp Ecklonia radiata canopy

Thallose red algae Ballia callitricha

Red coralline algae Haliptilon roseum

Green algae Caulerpa flexilis

Encrusting coralline algae around crayweed P. comosa holdfast

Figure 1.1 Examples of macroalgae found on subtidal reefs on the Victorian coast.

Grazing and predatory mobile invertebrates are prominent animal inhabitants of the reef (Figure 1.2). Common grazers include blacklip and greenlip abalone Haliotis rubra and H. 2



laevigata, warrener Turbo undulatus and sea urchins Heliocidaris erythrogramma, Holopneustes species and Amblypneustes species. These species can influence the growth and survival of habitat forming species. For example, sponges and foliose seaweeds are often prevented from growing on encrusting coralline algae surfaces through the grazing actions of abalone and sea urchins. Predatory invertebrates include dogwhelks Dicathais orbita, southern rock lobster Jasus edwardsii, octopus Octopus moarum and a wide variety of sea star species. Other large reef invertebrates include mobile filter feeding animals such as feather stars Cenolia trichoptera and sessile (attached) species such as sponges, corals, bryozoans, hydroids and ascidians. Fishes are also a dominant component of reef ecosystems, in terms of both biomass and ecological function (Figure 1.3). Reef fish assemblages include roaming predators such as blue-throated wrasse Notolabrus tetricus, herbivores such as herring cale Odax cyanomelas, planktivores such as sea sweep Scorpis aequipinnis and picker-feeders such as six-spined leatherjacket Meuschenia freycineti. The type and abundance of each fish species varies considerably, depending on exposure to swell and waves, depth, currents, reef structure, seaweed habitat structure and many other ecological variables. Many fish species play a substantial ecological role in the functioning and shaping of the ecosystem. For example, the feeding activities of fishes such as scalyfin Parma victoriae and magpie morwong Cheilodactylus nigripes promote the formation of open algal turf areas, free of larger canopyforming seaweeds. Although shallow reef ecosystems in Victoria are dominated, in terms of biomass and production, by seaweeds, mobile invertebrates and fishes, there are many other important biological components to the reef ecosystem. These include small species of crustaceans and molluscs from 0.1 to 10 mm in size, occupying various niches as grazers, predators or foragers. At the microscopic level, films of microalgae and bacteria on the reef surface are also important. Victoria’s shallow reefs are a very important component of the marine environment because of their high biological complexity, species diversity and productivity. Subtidal reef habitats also have important social and cultural values, which incorporate aesthetic, recreational, commercial and historical aspects. Shallow subtidal reefs also have significant economic value, through commercial fishing of reef species such as wrasses, morwong, rock lobster, abalone and sea urchins, as well as recreational fishing, diving and other tourism activities.

3


Southern rock-lobster Jasus edwardsii


Red bait crab Plagusia chabrus

Blacklip abalone Haliotis rubra

Feather star Cenolia trichoptera

Nectria ocellata

Heliocidaris erythrogramma

Fromia polypora

Red velvet fish Gnathanocanthus goetzeei

4



Figure 1.2 Examples of species of invertebrates and cryptic fish found on Victorian subtidal reefs.

Sea sweep Scorpis aequipinnis and

Scalyfin Parma victoriae

butterfly perch Caesioperca lepidoptera

Blue-throated wrasse Notolabrus tetricus

Six-spined leatherjacket Meuschenia freycineti (male)

Magpie morwong Cheilodactylus nigripes

Old-wife Enoplosus armatus

Figure 1.3 Examples of fish species found on Victorian subtidal reefs

5



1.2 Subtidal Reef Monitoring Program 1.2.1 Objectives An important aspect of the management and conservation of Victorian marine natural resources and assets is assessing the condition of the ecosystem and how this changes over time. Combined with an understanding of ecosystem processes, this information can be used to manage any threats or pressures on the environment to ensure ecosystem sustainability. Consequently, the Victorian Government has established a long-term Subtidal Reef Monitoring Program (SRMP). The primary objective of the SRMP is to provide information on the status of Victorian reef flora and fauna (focussing on macroalgae, macroinvertebrates and fish). This includes monitoring the nature and magnitude of trends in species abundances, species diversity and community structure. This is achieved through regular surveys at locations throughout Victoria, encompassing both representative and unique habitats and communities. Information from the SRMP allows managers to better understand and interpret long-term changes in the population and community dynamics of Victoria’s reef flora and fauna. As a longer time series of data is collected, the SRMP will allow managers to: compare changes in the status of species populations and biological communities between highly protected marine national parks and marine sanctuaries and other Victorian reef areas (e.g. Edgar and Barrett 1997, 1999); determine associations between species and between species and environmental parameters (e.g. depth, exposure, reef topography) and assess how these associations vary through space and time (e.g. Edgar et al. 1997; Dayton et al. 1998; Edmunds, Roob & Ferns 2000); provide benchmarks for assessing the effectiveness of management actions, in accordance with international best practice for quality environmental management systems (Holling 1978; Meredith 1997); and determine the responses of species and communities to unforeseen and unpredictable events such as marine pest invasions, mass mortality events, oil spills, severe storm events and climate change (e.g. Ebeling et al. 1985; Edgar 1998; Roob et al. 2000; Sweatman et al. 2000). A monitoring survey gives an estimate of population abundance and community structure at a small window in time. Patterns seen in data from periodic surveys are unlikely to exactly match changes in the real populations over time or definitively predict the size and nature of future variation. Plots of changes over time are unlikely to match the changes in real 6



populations because changes over shorter time periods and actual minima and maxima may not be adequately sampled (Figure 1.4). Furthermore, because the nature and magnitude of environmental variation is different over different time scales, variation over long periods may not be adequately predicted from shorter-term data. Sources of environmental variation can operate at the scale of months (e.g. seasonal variation), years (e.g. el Niño), decades (e.g. extreme storm events) or even centuries (e.g. global warming). Other studies indicate this monitoring program will begin to adequately reflect average trends and patterns as the surveys continue over longer periods (multiple years to decades). Results always need to be

Parameter

interpreted within the context of the time scale over which they have been measured.

Time Figure 1.4 An example plot depicting change in an environmental, population or community variable over time (days, months or years). The black circles denote examples of monitoring times. Note how data from these times may not necessarily reflect patterns over shorter time periods, or true maxima or minima over longer time periods. Note further how data from any window of 2 or 3 consecutive monitoring times fails to adequately estimate the patterns or variation over the longer time period.

1.2.2 Monitoring Protocols and Locations The SRMP uses standardised underwater visual census methods based on an approach developed and applied in Tasmania by Edgar and Barrett (1997). Details of standard operational procedures and quality control protocols for Victoria’s SRMP are described in Edmunds and Hart (2003). The SRMP was initiated in May 1998 with 15 sites established on subtidal reef habitats in the vicinity of Port Phillip Heads Marine National Park. In 1999 the SRMP was expanded to reefs 7



in the vicinity of the Bunurong Marine National Park (12 sites), Phillip Island (6 sites), and Wilsons Promontory Marine National Park (20 sites). In 2003, the Subtidal Reef Monitoring Program was expanded to include a further seven Marine National Parks and Marine Sanctuaries: Point Cook, Jawbone, Ricketts Point, Merri, Marengo Reef and Eagle Rock Marine Sanctuaries and Point Addis Marine National Park.

1.2.3 Monitoring in Western Victoria Marine Sanctuaries This report describes the subtidal reef monitoring program and the results from the first survey of subtidal reefs on the west coast of Victoria, including at Point Addis Marine National Park and Merri, Marengo Reefs and Eagle Rock Marine Sanctuaries. The objectives of this report are to: 1. provide an overview of the methods used for the SRMP; 2. provide general descriptions of the biological communities and species populations at each monitoring site in December 2003 and January 2004; 3. identify any unusual biological phenomena such as interesting or unique communities or species; and 4. identify any introduced species at the monitoring locations.

8



2.0 METHODS 2.1 Site Selection and Survey Times Ten monitoring sites were established on western Victorian subtidal reefs between December 2003 and January 2004 (Tables 2.1 and 2.2). Two monitoring sites were located inside and two sites outside the Point Addis Marine National Park and one site inside and one site outside Eagle Rock, Marengo Reefs and Merri Marine Sanctuary. Monitoring sites were located on representative subtidal reef habitat in each area.

2.1.1 Point Addis Marine National Park Point Addis Marine National Park is in the Central Victorian bioregion (Figure 2.1). It is located approximately between Bells Beach and Anglesea, east of Cape Otway. Point Addis is a prominent headland in the middle of the park. Subtidal reefs in this location are predominantly sandstone and limestone. Monitoring sites inside Point Addis Marine National Park were established at two offshore reefs known locally as Ingoldsby Reef and The Olives. Ingoldsby Reef is near the western edge of the park. A monitoring site was located on the inshore side of this reef along the 4 m depth contour (Ingoldsby Inside, Site 3906). The Olives reef is located towards the centre of the park. A monitoring site was established here along the 7 m depth contour, also on the shoreward side of the reef (The Olives, Site 3905). Two reference sites were established outside the protected area. The first reference site is approximately 2 km southwest of the park, offshore from Anglesea and is known as Anglesea Reef (Site 3907). A second reference site was established east of the park, offshore from Torquay. This site is known as Phyco’s (or phycologists’) Reef (Site 3908) because of the diverse algal assemblage encountered. The survey site at Phyco’s Reef was at 8 m depth.

9



-38.300

-38.320

Pt Danger 3908

-38.340

-38.360

Latitude

-38.380

Pt Addis

-38.400 Anglesea 3907

3906

3905

-38.420 Pt Roadkni ght

-38.440

-38.460

Bass Strait -38.480 0 1 2 Kilometres -38.500 144.200

144.250

144.300

144.350

144.400

Longitude

Figure 2.1 Location of monitoring sites inside and outside the Point Addis Marine National Park. The park boundary is outlined, with circles representing monitoring sites.

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2.1.2 Eagle Rock Marine Sanctuary Eagle Rock Marine Sanctuary is a small marine protected area near Fairhaven, southwest of Point Addis in the Central Victorian Bioregion (Figure 2.2). Subtidal reef habitats of basalt and sandstone within the marine sanctuary are patchy and interspersed with large areas of bare sand. Reef habitats may be more continuous closer to shore but these areas could not be surveyed because of shallow water and prevailing swell conditions. A monitoring site, Eagle Rock Inside (Site 3909), was established along the 5 m depth contour over patchy reef and sand close to Eagle and Table Rocks. A reference monitoring site, Eagle Rock Outside (Site 3910), was located on similar, but more continuous, reef habitat outside the eastern boundary of the sanctuary. This site was along the 7 m depth contour.

-38.466

Aireys Inlet

-38.468

e d u itt a L

Eagle Rock

-38.470

3909

Split Point

3910

Table Rock

-38.472

-38.474 0

144.098

144.100

144.102

144.104

144.106

144.108

100 200 Metres

144.110

144.112

Longtitude

Figure 2.2 Location of monitoring sites inside and outside the Eagle Rock Marine Sanctuary. The park boundary is outlined and the monitoring sites are represented by circles.

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2.1.3 Marengo Reefs Marine Sanctuary The Marengo Reefs Marine Sanctuary is located a short distance south of Apollo Bay, approaching the western boundary of the Central Victorian Bioregion (Figure 2.3). The reefs within the sanctuary consist of two rocky sandstone platforms separated by a small gutter. The platforms are a short distance offshore and large areas of reef are exposed at low tide. A monitoring site, Marengo Reef (Site 3911), was established along the 3 m depth contour on the northern (inshore) side of the Marengo Reefs. The site consists of relatively flat slabs of sandstone reef. A reference monitoring site, Barnham Black (Site 3912), was established less than 1 km north of the Marengo Reef site along the 6 m depth contour. This site was on more complex reef with depressions, cracks and crevices and small rocky pinnacles.

-38.760

Apollo Bay Bunbury Point 3912

-38.765

Latitude

-38.770

Mounts Bay

-38.775

3911 -38.780

Hayley Point

-38.785

0 -38.790 143.650

143.655

143.660

143.665

143.670

143.675

143.680

250 500 Metres

143.685

143.690

Longitude

Figure 2.3 Location of monitoring sites inside and outside the Marengo Reefs Marine Sanctuary. The park boundary is outlined and the monitoring sites are represented by circles.

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2.1.4 Merri Marine Sanctuary Merri Marine Sanctuary is in the Otway Bioregion on the west coast of Victoria near Warrnambool (Figure 2.4). Coastal reefs at Merri are either patchy and interspersed with areas of sand, or more consolidated hard reef cut by deeper depressions and large crevices (to 15 m). A monitoring site, Merri (Site 3701), was established inside the marine sanctuary close to Middle Island along the 8 m depth contour. The site covers areas of patchy reef and sand, as well as more continuous reef with deep sections. A reference monitoring site, Breakwater (Site 3702), was located at the southeast of the sanctuary near Breakwater Rock along the 5m depth contour. The reef here is continuous and slightly undulating.

-38.400

-38.402

Pickering Point

Latitude

-38.404 Middle

3701

Island

Breakwater Rock

-38.406 3702 -38.408

0 -38.410 142.460

142.464

142.468

142.472

142.476

100 200 Metres 142.480

Longtitude

Figure 2.4 Location of monitoring sites inside and outside the Merri Marine Sanctuary. The park boundary is outlined and the monitoring sites are represented by circles.

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Table 2.1 Subtidal reef monitoring sites on the west coast of Victoria Marine Protected Area

Site No.

Site Name

MPA/Reference

Depth (m)

Point Addis

3905

The Olives

MPA

7

Point Addis

3906

Ingoldsby Inside

MPA

4

Point Addis

3907

Anglesea Reef

Reference

3

Point Addis

3908

Phyco’s Reef

Reference

8

Eagle Rock

3909

Eagle Rock Inside

MPA

5

Eagle Rock

3910

Eagle Rock Outside

Reference

7

Marengo Reefs

3911

Marengo Reef

MPA

3

Marengo Reefs

3912

Barnham Black

Reference

6

Merri

3701

Merri

MPA

8

Merri

3702

Breakwater

Reference

5

Table 2.2 Survey times for subtidal reef monitoring on the western coast of Victoria. Marine Protected Area

Season

Survey Period

Point Addis

Summer

December 2003

Eagle Rock

Summer

December 2003

Marengo Reefs

Summer

January 2004

Merri

Summer

January 2004

2.2 Census Method 2.2.1 Transect Layout The visual census methods of Edgar and Barrett (Edgar & Barrett 1997, 1999; Edgar et al. 1997) are used for this monitoring program as they are non-destructive and provide quantitative data on a large number of species, and the structure of the reef communities. The Edgar-Barrett method is also used in Tasmania, New South Wales and Western Australia. The adoption of this method in Victoria provides a systematic and comparable approach to monitoring reefs in southern Australia. The surveys in Victoria are in accordance with a standard operational procedure to ensure long-term integrity and quality of the data (Edmunds and Hart 2003). At most monitoring locations in Victoria, surveying along the 5 m depth contour is considered optimal because diving times are not limited by decompression schedules and these reefs are of interest to natural resource managers. However, the actual depth that can be surveyed varies with reef extent, geomorphology and exposure. Monitoring sites along the western coast of Victoria are between 3 and 8 m deep. Each site is located using differential GPS and marked with a buoy or the boat anchor. A 100 m numbered and weighted transect line is run along the appropriate depth contour either 14



side of the central marker. The resulting 200 m of line is divided into four contiguous 50 m sections (T1 to T4). The orientation of transect is the same for each survey, with T1 generally toward the north or east (i.e. anticlockwise along the coast). For each transect, three different census methods were used to obtain adequate descriptive information on reef communities at different spatial scales. These involved the census of: (1) the abundance and size structure of large fishes; (2) the abundance of cryptic fishes and benthic invertebrates; and (3) the percent cover of macroalgae and sessile invertebrates. Over 100 species were observed during the monitoring program along the western coast of Victoria (Tables 2.3 and 2.4). The depth, horizontal visibility, sea state and cloud cover are recorded for each site. Horizontal visibility is gauged by the distance along the transect line to detect a 100 mm long fish. All field observations are recorded on underwater paper.

2.2.2 Method 1 – Mobile Fishes and Cephalopods The densities of mobile large fishes and cephalopods are estimated by a diver swimming up one side of a 50 m section of the transect, and then back along the other. The diver records the number and estimated size-class of fish, within 5 m of each side of the line. The sizeclasses for fish are 25, 50, 75, 100, 125, 150, 200, 250, 300, 350, 375, 400, 500, 625, 750, 875 and 1000+ mm. Each diver has size-marks on their underwater slate to enable calibration of their size estimates. A total of four 10 x 50 m sections of the 200m transect are censused for mobile fish at each site. The data for easily sexed species are recorded separately for males and female/juveniles. Such species include the blue-throated wrasse Notolabrus tetricus, herring cale Odax cyanomelas, barber perch Caesioperca rasor, rosy wrasse Pseudolabrus psittaculus and some leatherjackets.

2.2.3 Method 2 – Invertebrates and Cryptic Fishes Cryptic fishes and megafaunal invertebrates (non-sessile: e.g. large molluscs, echinoderms, crustaceans) are counted along the transect lines used for the fish survey. A diver counts animals within 1 m of one side of the line (a total of four 1 x 50 m sections of the 200 m transect). A pole carried by the diver is used to standardise the 1 m distance. The maximum length of abalone is measured in situ using vernier callipers whenever possible. Selected specimens are collected for identification and preservation in a reference collection.

2.2.4 Method 3 – Macroalgae and Sessile Invertebrates The area covered by macroalgal and sessile invertebrate species is quantified by placing a 0.25 m2 quadrat at 10 m intervals along the transect line and determining the percent cover of the all plant species. The quadrat is divided into a grid of 7 x 7 perpendicular wires, giving 50 points (including one corner). Cover is estimated by counting the number of times each species occurs directly under the 50 positions on the quadrat (1.25 m2 for each of the 50 m 15



sections of the transect line). Selected specimens are collected for identification and preservation in a reference collection.

2.2.5 Method 4 – Macrocystis In addition to macroalgal cover, the density of Macrocystis angustifolia plants is estimated. While swimming along the 200 m transect line, a diver counts all observable plants within 5 m either side of the line, for each 10 m section of the transect (giving counts for 100 m2 sections of the transect). Table 2.3 Mobile fishes, including sharks and rays, surveyed using Method 1 and macroinvertebrates and cryptic fishes surveyed using Method 2 on the western coast of Victoria Method 1

Method 1

Method 2

Method 2

Mobile Sharks and Rays

Mobile Fishes (continued)

Crustacea

Echinodermata (continued)

H. portusjacksoni

Aplodactylus arctidens

Jasus edwardsii

Tosia australis

P. variolatum

Cheilodactylus nigripes

S. strigimanus

Pentagonaster dubeni

Dasyatis brevicaudata

C. spectabilis

Plagusia chabrus

Nectria ocellata

Mobile Fishes

Dactylophora nigricans

Mollusca

Nectria macrobranchia

T. caudimaculatus

Latridopsis forsteri

Haliotis rubra

Petricia vernicina

Dinolestes lewini

Achoerodus gouldii

Haliotis laevigata

Fromia polypora

Pseudocaranx dentex

Dotalabrus aurantiacus

Scutus antipodes

Plectaster decanus

U. vlaminghii

Notolabrus tetricus

Turbo undulatus

Echinaster arcystatus

Pempheris multiradiata

Notolabrus fucicola

Cabestana spengleri

Nepanthia troughtoni

Girella tricuspidata

P. psittaculus

Dicathais orbita

Patiriella brevispina

Girella zebra

Pictilabrus laticlavius

Pleuroploca australasia

C. muricata

Scorpis aequipinnis

Odax cyanomelas

Penion mandarinus

H. porosissimus

Scorpis lineolata

Haletta semifasciata

Conus anemone

H. erythrogramma

Atypichthys strigatus

Acanthaluteres vittiger

S. ornatum

Cryptic Fishes

Tilodon sexfasciatus

Meuschenia freycineti

Tambja verconis

P. variolatum

Enoplosus armatus

M. flavolineata

C. tasmaniensis

Aetapcus maculatus

Parma victoriae

M. hippocrepis

Octopus maorum

Bovichtus angustifrons

Meuschenia galii

Echinodermata

Heteroclinus johnstoni

Aracana aurita

Cenolia trichoptera

B. jacksonianus

Diodon nichthemerus

Cenolia tasmaniae

16



Table 2.4 Macroalgae (Method 3) surveyed on the western coast of Victoria Method 3

Method 3

Method 3

Method 3

Chlorophyta (green algae)

Phaeophyta (brown algae, continued)

Rhodophyta (red algae)

Rhodophyta (red algae, continued)

Ulva spp

Perithalia cordata

Gelidium asperum

Acrotylus australis

Caulerpa longifolia

Ecklonia radiata

Gelidium australe

Curdiea angustata

C. scalpelliformis

M. angustifolia

Pterocladia lucida

Melanthalia obtusata

Caulerpa brownii

Durvillaea potatorum

Asparagopsis armata

Melanthalia abscissa

Caulerpa obscura

X. chondrophylla

Delisea pulchra

Plocamium angustum

Caulerpa flexilis

Phyllospora comosa

M. flabellata

Plocamium costatum

C. flexilis var. muelleri

Seirococcus axillaris

Amphiroa anceps

Plocamium mertensii

Caulerpa geminata

Acrocarpia paniculata

Arthrocardia wardii

Plocamium dilatatum

Caulerpa simpliciuscula

Cystophora platylobium

Haliptilon roseum

P. preissianum

Codium duthieae

C. moniliformis

C. sagittatum

P. cartilagineum

Codium spp

Cystophora xiphocarpa

M. radiatum

P. leptophyllum

Filamentous greens

Cystophora pectinata

Encrusting corallines

Erythrymenia minuta

Cystophora monilifera

Corallines unidentified

Rhodymenia australis

Phaeophyta (brown)

Cystophora retorta

Gigartina sp.

R. leptophylla

Halopteris spp

Cystophora siliquose

Hypnea ramentacea

Rhodymenia obtusa

C. spongiosus

Cystophora retroflexa

Hypnea sp.

Rhodymenia spp

Dictyota dichotoma

C. confluens

Callophyllis lambertii

Cordylecladia furcellata

P. paniculatum

Sargassum decipiens

Callophyllis rangiferina

Ballia callitricha

Lobospira bicuspidata

Sargassum sonderi

Nizymenia australis

Euptilota articulata

C. microphylla

Sargassum varians

Sonderopelta coriacea

Martensia australis

H. sinclairii

S.verruculosum

S. sp. /Peyssonelia

Hemineura frondosa

Zonaria turneriana

Sargassum vestitum

P. peperocarpus

L. marginata

Glossophora nigricans

S. spinuligerum

Callophycus laxus

Laurencia elata

Carpomitra costata

Sargassum spp

Erythroclonium sonderi

Laurencia filiformis

Areschougia congesta

Echinothamnion hystrix Thuretia quercifolia

2.3 Data Analysis To identify changes and trends within marine protected areas, sites from inside each MPA will be compared to paired reference sites outside each MPA. For the first survey, data from all sites is compared together. This allows an assessment of biota at each site to be placed in a bioregional context. Descriptions of the biota and community structure at each site are also provided.

17



2.3.1 Community Structure Community structure is a function of both the species present and the abundance of each species. The community structure between pairs of samples was compared using the BrayCurtis dissimilarity coefficient. This index compares the abundance of each species between two samples to give a single value of the difference between the samples, expressed as a percentage (Faith et al. 1987; Clarke 1993). Prior to analysis, the data were log transformed to weight down the influence of highly abundant species in describing community structure, giving a more even weighting between abundant and rarer species (following abundance transformations by Sweatman et al. 2000). The Bray-Curtis dissimilarity index was calculated for all possible combinations of sites. This resulted in a matrix of pair-wise comparisons known as a dissimilarity matrix. The dissimilarity matrix is also termed a distance matrix as it effectively represents distances between samples in hyper-dimensional space. The dissimilarity matrix was used for all analyses of community structure in this study.

2.3.2 Depiction of Community Differences The hyper-dimensional information in the dissimilarity matrix was simplified and depicted using non-metric multidimensional scaling (MDS; Clarke 1993). This ordination method finds the representation in fewer dimensions that best depicts the actual patterns in the hyperdimensional data (i.e. reduces the number of dimensions while depicting the salient relationships between the samples). The MDS results were then depicted graphically to show differences between the replicates at each location. The distance between points on the MDS plot is representative of the relative difference in community structure. Kruskall stress is an indicator statistic calculated during the ordination process and indicates the degree of disparity between the reduced dimensional data set and the original hyperdimensional data set. A guide to interpreting the Kruskal stress indicator is given by Clarke (1993): (< 0.1) a good ordination with no real risk of drawing false inferences; (< 0.2) can lead to a usable picture, although for values at the upper end of this range there is potential to mislead; and (> 0.2) likely to yield plots which can be dangerous to interpret. These guidelines are simplistic and increasing stress is correlated with increasing numbers of samples. Where high stress was encountered with a two-dimensional data set, threedimensional solutions were sought to ensure an adequate representation of the higherdimensional patterns.

18



2.3.3 Trends in Community Structure Trends cannot be examined in this report since only one survey has been completed at each site along the west coast of Victoria. Trends in community structure will be examined when further surveys have been completed at each location.

2.3.4 Species Diversity Species diversity involves the consideration of two components: species richness and evenness. Species richness is the number of species present in the community while evenness is the degree of similarity of abundances between species. If all species in a community have similar abundances, then the community has a high degree of evenness. If a community has most of the individuals belonging to one species, it has low evenness. Species diversity is a combination of species richness and the relative abundance of each species, and is often referred to as species heterogeneity. Measures of diversity give an indication of the likelihood that two individuals selected at random from a community are different species. Species richness (S) was enumerated by the total species count per site. This value was used for calculation of evenness and heterogeneity statistics. Species diversity (i.e. heterogeneity among species) was described using the reciprocal of Simpson’s index (1/DSimpson = Hill’s N2). This value describes species diversity as a combination of species richness (i.e. the number of species) and species evenness (i.e. the equitability of the abundances of the species). The value varies between 1 and s (i.e. the total number of species in the sample) with higher values indicating higher diversity. In general, Hills N2 gives an indication of the number of dominant species within a community. Hills N2 provides more weighting for common species, in contrast to indices such as the Shannon-Weiner Index (Krebs 1999), which weights the rarer species. The weighting of common species was considered more appropriate for this study because the sampling regime is designed to target the more common species. Simpson's index of evenness (E1/D) was used to describe the equitability of abundances between species. Higher values of Simpson’s index indicate that all species occur in more even abundances. This index is relatively unaffected by rare species in the sample (Krebs 1999).

2.3.5 Species Populations The abundance of each species was summarised by calculating total counts of fish and invertebrates and total percentage cover of macroalgae, for each site.

19



The population size structure for blacklip abalone Haliotis rubra was assessed by calculating mean lengths and size frequency curves. The size structure of the common fishes bluethroated wrasse Notolabrus tetricus, purple wrasse Notolabrus fucicola, herring cale Odax cyanomelas and scalyfin Parma victoriae was examined using mean lengths and frequency tables.

Figure 2.5 Biologist-diver with transect reel, Lonsdale Back Beach.

Figure 2.6 The cover of macrophytes is measured by the number of points intersecting each species on the quadrat grid.

20



3.0 MACROALGAE 3.1 Species Richness and Diversity Algal species richness was relatively high at the four sites surveyed along the Point Addis coast (inside and outside the Marine National Park) and near Merri Marine Sanctuary further west (Table 3.1). In these areas the number of species recorded varied between 34 and 46. Sites inside and outside Eagle Rock and Marengo Reefs Marine Sanctuaries had relatively lower species richness. The number of brown and green algal species was similar between all sites. Therefore, differences in the number of species of red algae generally explain differences in species richness between areas and sites; i.e. areas with high numbers of red algal species have a relatively high species richness. Ingoldsby Inside (Site 3906) had the highest species richness. At this site there was a large number of red algal species combined with a higher number of understorey brown algal species such as Clanidophora microphylla and Glossophora nigricans and four species of the green alga Caulerpa. Lowest species richness occurred at Eagle Rock Inside (Site 3909). This was because of the limited area of continuous reef available to survey which resulted in large amounts of sand in the survey quadrats. Patterns in species diversity were similar to those described for species richness, with highest diversity along the Point Addis coast (inside and outside the Marine National Park) and near Merri Marine Sanctuary further west (Table 3.1). Lower diversity was recorded inside and outside Eagle Rock and Marengo Reefs Marine Sanctuaries. Sites with lower diversity tended to have an overstorey dominated by Phyllospora comosa with relatively few understorey species. Sites with higher diversity tended to have an overstorey dominated by Ecklonia radiata or had a mixed overstorey with E. radiata, P. comosa as well as Seirococcus axillaris and Acrocarpia paniculata. These sites had higher numbers and more diverse understorey (small reds and browns) algal assemblages.

21



Table 3.1 Diversity statistics for algae on the western coast of Victoria during the first survey: pooled values for number of species, heterogeneity and species evenness for each site. Site

Species Richness

Heterogeneity

Evenness

1/D=N2

E1/D

Merri

42

13.83

0.33

Breakwater

34

8.26

0.24

The Olives

41

7.91

0.19

Ingoldsby Inside

46

9.00

0.20

Anglesea Reef

40

7.20

0.18

Phyco’s Reef

38

8.36

0.22

Eagle Rock Inside

18

2.45

0.14

Eagle Rock Outside

34

5.51

0.16

Marengo Reef

24

1.77

0.07

Barnham Black

22

2.11

0.10

3.2 Community Structure The algal communities surveyed on the western coast of Victoria were similar in species composition and community structure to those surveyed in other exposed coastal locations along the Victorian coast (e.g. Edmunds et al. 2003). Sites tended to have a relatively high cover of large brown algal species forming an overstorey, however, the dominant overstorey species varied between locations (Table 3.2). Various green, brown and red algal species, including encrusting coralline algae, form an understorey below the brown algal canopy. The MDS plots of dissimilarities in algal assemblage structure showed clear grouping of some sites (Figure 3.1). Sites along the Point Addis coast (Sites 3905-3908) grouped relatively closely together, along with the Merri sites (Sites 3701 and 3702) and Eagle Rock Outside (Site 3910). The Point Addis sites were distinguished from other sites by the absence of an algal canopy dominated by crayweed Phyllospora comosa. The canopy was instead dominated by common kelp Ecklonia radiata and/or Seirococcus axillaris and Acrocarpia paniculata. There was relatively low level cover of other medium to large browns, which included species such as Cystophora retroflexa and various Sargassum species. In contrast to other sites in this group there was no species of Cystophora at Phyco’s Reef (Site 3908). Understorey species at each of these sites included the green Caulerpa flexilis var. muelleri. (up to 8 % cover at Ingoldsby Inside; Site 3906) and reds, particularly the corraline alga Haliptilon roseum and smaller fleshy red algae Ballia callitricha, Phacelocarpus peperocarpus and Plocamium spp. Encrusting corraline algae cover varied between 6.6 and 14.5 % at these sites. There was a relatively high cover of Amphibolis antartica reflecting high levels of sediment along some sections of the survey transect at Anglesea Reef (Site 3907). 22



3907 3909 3906

3911

3905 3701

3702

3908 3910

3912

Figure 3.1 MDS plot of algal assemblage structure on the west coast of Victoria December 2003January 2004. The numbers on each plot denote the survey site. Kruskall stress = 0.08.

Merri (Site 3701) and Breakwater (Site 3702) grouped closely together with the Point Addis sites (Figure 3.1). The algal canopy at Merri and Breakwater was dominated by P. comosa (23 - 38 % cover) combined with a lower cover of Ecklonia radiata and Acrocarpia paniculata. Other medium to large browns were absent. There was a relatively low cover of smaller browns, except for Perithalia caudata at Breakwater. The understorey was dominated by a relatively diverse assemblage of fleshy red algae which also had a relatively high cover. Dominant species included Gelidium australe, Pterocladia lucida, Delisea pulchra, Phacelocarpus peperocarpus and Ballia callitricha. There was 11 % and 18 % cover of encrusting corallines at Merri and Breakwater respectively. Eagle Rock Outside (Site 3910), which grouped closely with the Point Addis and Merri sites in MDS, had an algal canopy dominated by Phyllospora comosa with smaller contributions to cover made by Ecklonia radiata and Seirococcus axillaris. While diverse, other brown algal species contributed little to overall algal cover. Understorey species with relatively high cover included the green alga Codium duthieae and the red algal species Phacelocarpus

23



peperocarpus, Melanthalia obtusata and Ballia callitricha. Encrusting corralines had a cover of 5.4 % at Eagle Rock Outside. Eagle Rock Inside (Site 3909) and Marengo Reef (Site 3911) grouped closely together in the top left corner of the MDS plot, separate from all other sites. These sites had similar species composition but different community structure. At both sites the canopy was formed by Phyllospora comosa. This species had 44 % cover at Eagle Rock Inside and 83 % cover at Marengo Reef. There was a relatively diverse assemblage of smaller brown algal species with a Cystophora moniliformis and Cystophora retorta contributing a combined cover up to 8 %. There were very few species and very low cover of red and green algae at both sites. Encrusting corraline algae had a cover of 12.8 % and 23 % at Eagle Rock Inside and Marengo Reef respectively. These two sites had the highest levels of sand of all sites surveyed. The high levels of sand would contribute to the relatively low diversity. Barnham Black (reference site for Marengo Reefs MS; Site 3912) was separate from all other sites when represented by MDS (Figure 3.1). The algal canopy at this site was composed of Phyllospora comosa, which had very high cover, as well as Acrocarpia paniculata. There was low diversity and cover of other species of brown algae. A few corraline and thallose reds contributed some understorey cover including Haliptilon roseum, Plocamium angustum and P. dilatatum. There were three species of the green alga Caulerpa not observed at any other sites during this survey. These were Caulerpa obscura, C. flexilis and C. geminata.

24



Table 3.2 Macroalgal abundance (percent cover) at each monitoring site on the western coast of Victoria. Surveys occurred between December 2003-January 2004. Species

Site 3701

3702

3905

3906

3907

1.1

0.1

0.1

3908

3909

3910

3911

3912

0.1

0.3

Chlorophyta – Green Algae Ulva spp

0.1

Caulerpa scalpelliformis 6.4

Caulerpa longifolia

0.2

Caulerpa brownii

0.5

0.3

0.2

0.2

Caulerpa obscura

2.8

Caulerpa flexilis

0.9

C. flexilis var. muelleri

1.4

4.3

6.9

7.8

1.6

1.3 0.5

Caulerpa geminata 1.2

Caulerpa simpliciuscula

1.7 6.3

Codium duthieae Codium spp

3.1 0.5

Filamentous greens Phaeophyta – Brown Algae Halopteris spp

3.6

2.5

2.1

1.8

0.7

Cladostephus spongiosus Dictyota dichotoma

0.3

3

Lobospira bicuspidata

0.3

C. microphylla

0.2

Homeostrichus sinclairii

2.1

1.8

Zonaria turneriana

2

0.5

0.3

2.5

2.9

4.1

0.7

0.2

0.9

0.1

1.7

0.2

0.3

0.1

1.9

0.8 2.7

1.2

1

0.5

0.5

0.4 0.6

0.3

0.2 1.2

1.5

1.8

1.1

1.2

0.9

0.5

Glossophora nigricans Carpomitra costata

0.7

Perithalia cordata

4.1

12.9

Ecklonia radiata

14

5.4

0.3 2 41.2

32.1

0.4 9.8

41.9

8.3

2.3

Macrocystis angustifolia

2.5

Durvillaea potatorum 1.1

Xiphophora chondrophylla 23.3

38.7

Seirococcus axillaris Acrocarpia paniculata

12.2

Cystophora platylobium

0.4

Cystophora moniliformis

1.3

0.4

Pachydictyon paniculatum

Phyllospora comosa

1.1

7.7

43.8 10

15

21.5

20.1

11.8

7.6

2.1

4.6

52.2

82.9

78.4

1.1

12.6

4.1 2.5 1.1

1.7

2

5.2

3.5

1.6

0.9

Cystophora xiphocarpa 6.7

Cystophora pectinata 0.3

Cystophora monilifera

0.5

Cystophora retorta

25

2.8

2.2



Table 3.2 (continued) Macroalgal abundance (percent cover) at each monitoring site on the western coast of Victoria. Surveys occurred between December 2003-January 2004. Species

Site 3701

3702

3905

Cystophora siliquosa 0.7

Cystophora retroflexa Carpoglossum confluens

3906

3907

0.8

0.4

2.1

0.7

0.4

3908

3909

3910

3911

3912

1.3

1.5

2.5

1.5

Sargassum decipiens 0.7

Sargassum sonderi

0.3

1.6

0.3

Sargassum varians

0.4

Sargassum verruculosum 0.9

Sargassum vestitum

2.6

1.8

Sargassum spinuligerum 1.1

Sargassum spp Brown algae unidentified

0.5

3

0.2

1.1 0.3

0.3

0.4

2.6

0.6

2.1 0.2

Rhodophyta – Red Algae Gelidium asperum

6.8

Gelidium australe

0.3

Pterocladia lucida

8.2

0.5 3.8

Asparagopsis armata Delisea pulchra

3.6

1.4

M. flabellate

2.8

1.2

Amphiroa anceps

0.2

4 0.9

0.3

0.8

3.3

0.6

0.3

1.5

2

6.1

2.4

3.5

6.2

0.5

Arthrocardia wardii Haliptilon roseum

1.4

6

4.7

3.7

2

Cheilosporum sagittatum

0.7

0.3

0.4

1.1

1.3

Metagoniolithon radiatum

0.7

1.3

1

0.6

Encrusting corallines

11.1

18.2

14

6.6

1.8 2.3

0.5

0.2

Nizymenia australis

2.1

1.9

1.1

Sonderopelta coriacea

2.8

0.6

Sonderopelta/Peyssonelia

0.8

0.7

0.3

P. peperocarpus

2.2

3.1

1.3

6.9

4.5

2.6

4

4.7

0.3 0.6 9.7

12.8

5.4

0.9

2.8

0.1

2

0.8

0.4

0.2

4.5

6.1

0.4

Callophycus laxus

23

13.2

0.3 1.4

1.4

0.3 4.2

1.7 0.7 0.3

Acrotylus australis 1.2

Curdiea angustata 1.3

0.9

0.3

0.2

Erythroclonium sonderi

Melanthalia abscissa

2.5

2.3

Callophyllis rangiferina

Melanthalia obtusata

0.5

0.6

Callophyllis lambertii

Areschougia congesta

3.4

0.4

Gigartina sp. Hypnea ramentacea

14.5

5.2

0.6

2.4

0.3

0.2

1.2

26

0.8

5.4 1.1

0.5



Table 3.2 (continued) Macroalgal abundance (percent cover) at each monitoring site on the western coast of Victoria. Surveys occurred between December 2003-January 2004. Species Plocamium angustum

Site 3701

3702

3905

3906

3907

3908

0.5

3.4

3.6

2.6

1.4

6.1

0.3

0.2

0.5

0.1

0.2

2.5

2.9

3.3

0.1

5.7

0.4

2.6

2.3

0.7

7

1.9

0.3

2.2

Plocamium dilatatum Plocamium preissianum

2.1

Plocamium cartilagineum

3911

3912

2.8

0.3

4.3

0.3

3.5

3.5

0.2 0.1

Plocamium leptophyllum Erythrymenia minuta

3910

2.1

Plocamium costatum Plocamium mertensii

3909

0.6

0.3 1.3 0.2

Rhodymenia leptophylla Rhodymenia australis

0.3

Rhodymenia obtusa

0.2

0.4

1.3

1.7

0.4

2.4

0.3

Rhodymenia spp Cordylecladia furcellata

0.7

Ballia callitricha

9.2

6.1

8

3

4.6

8.5

4.1

1.2

Euptilota articulata

0.4

0.4

0.4

0.3

0.2

1.7

1.4

0.2

Hemineura frondosa

0.5 0.2

Lenormandia marginata Laurencia elata

0.3

0.9

0.6 0.1

Laurencia filiformis

0.4

Echinothamnion hystrix

0.8

Other thallose red alga

7.9

1.9

0.5 1.2

0.2

0.2 0.3

1.1

4.3

3.5

7.2

1.1

0.4

Seagrass 27

Amphibolis antarctica Sand

2.7

5

5

45

9.2

14.5

3.3 String Kelp Macrocystis Angustifolia The string kelp Macrocystis angustifolia can grow up to 10 m in height and form dense forests with a thick canopy floating on the surface. Consequently, M. angustifolia is a significant habitat forming species. (Figure 3.2). Macrocystis angustifolia occurred at three monitoring sites during this survey: Merri (3701), Breakwater (3702) and Anglesea Reef (3907). Low densities were detected at Merri and Anglesea with only two and four plants detected respectively. In contrast, moderate to high densities of M. angustifolia occurred along the first 30 metres of survey Transect 1. Along this stretch of transect there were approximately 47 plants per 100 m2. No further plants were detected at this site.

27



Figure 3.2 Toothbrush leatherjacket Acanthaluteres vittiger swimming between Macrocystis angustifolia plants

28



4.0 INVERTEBRATES AND CRYPTIC FISHES 4.1 Species Richness and Diversity Invertebrate species richness was relatively even across most sites, but varied between 7 and 16 species (Table 4.1). Highest species richness occurred at Barnham Black (Site 3912) and The Olives (Site 3905). The relatively high species richness at Barnham Black was a reflection of the nine species of mollusc found at this site. Lowest species richness occurred at Ingoldsby Inside (Site 3906) and Eagle Rock Inside (Site 3909). Species diversity was also relatively even between sites (Table 4.1). Highest diversity occurred at Anglesea Reef where a total of 14 invertebrate individuals were recorded of which 11 were different species. Lowest species diversity was recorded at Eagle Rock Inside (Site 3909), Ingoldsby Inside (Site 3906) and The Olives (Site 3905) had the lowest diversity principally because of the numerical dominance of one of two species at each of these sites: blacklip abalone Haliotis rubra and the periwinkle Turbo undulatus.

Table 4.1 Species richness and diversity of invertebrates on the west coast of Victoria Site

Individuals

Species

Heterogeneity

Evenness

N

S

1/D=N2

E1/D

Merri

25

10

5.17

0.52

Breakwater

156

13

3.04

0.23

The Olives

153

15

2.27

0.15

Ingoldsby Inside

191

9

2.18

0.24

Anglesea Reef

14

11

8.91

0.81

Phyco’s Reef

44

13

7.74

0.60

Eagle Rock Inside

372

7

1.15

0.16

Eagle Rock Outside

32

10

3.16

0.32

Marengo Reef

107

13

3.99

0.31

Barnham Black

279

16

3.37

0.21

4.2 Assemblage Structure There was no clear pattern in invertebrate assemblage structure for the sites monitored (Figure 4.1). There was, however, some loose grouping of paired monitoring sites associated with each marine national park or sanctuary. Assemblages inside and outside the Point Addis Marine National Park tended to group loosely together in the bottom right of the MDS plot and the Merri and Marengo Sites were relatively close together on the left side of the plot. There was, however, clear separation of invertebrate assemblages at Eagle Rock Inside and Outside (Sites 3909 and 3910). 29



3909 3910

3701

3907 3906

3702 3911

3905 3912 3908

Figure 4.1 MDS plot of invertebrate assemblage structure on the west coast of Victoria, December 2003-January 2004. The labels next to each point denote the survey site. Kruskall stress = 0.12

Despite the loose grouping of the Point Addis monitoring sites, there were considerable differences in invertebrate assemblage structure between each of these sites. The two sites within the MNP, The Olives (Site 3905) and Ingoldsby Inside (Site 3906), each had a single numerically dominant species of herbivorous gastropod, with considerably lower numbers of other invertebrates. The dominant species at The Olives (Site 3905) was blacklip abalone Haliotis rubra and the dominant species at Ingoldsby Inside (Site 3906) was the periwinkle Turbo undulatus. Large grazing gastropods did not feature prominently at the two reference sites outside Point Addis MNP, which had relatively low and even numbers of invertebrate species. Both the MNP and reference sites at Point Addis shared a relatively diverse assemblage of echinoderms. Species of echinoderm common to all of these sites were the featherstar Cenolia trichoptera and the seastars Nectria macrobranchia and Nepanthia troughtoni. The invertebrate assemblages at Eagle Rock (Sites 3909 and 3910) differed considerably in invertebrate abundance, species composition and community structure. Eagle Rock Inside (Site 3909) had few species of invertebrates but very large numbers of the periwinkle Turbo 30



undulatus. The predatory gastropod Dicathais orbita occurred in moderate to low numbers at this site and there were very low densities of echinoderms and crustaceans. Eagle Rock Outside (Site 3910) did not have any species that was clearly numerically dominant. The predatory gastropod Dicathais orbita occurred in moderate to low numbers; other gastropods were in low numbers. There were five species of echinoderm of which the biscuit star was most common (4 individuals). The invertebrate assemblages at the Marengo Reef sites (Site 3911 and 3912) were relatively similar. These sites had many species in common and broadly similar relative proportions of each species in the assemblage. Blacklip abalone Haliotis rubra was the most abundant species at both sites although numbers were considerably higher at Barnham Black (Site 3912). The periwinkle Turbo undulatus was also relatively common at both sites. Other species of molluscs occurring at both sites were the elephant snail Scutus antipodes and the predatory gastropods Dicathais orbita and Pleuroploca australiasia. The species of echinoderm were the same at both sites but numbers of individuals varied. The featherstar Cenolia trichoptera and the velvet star Patiriella brevispina were common at Barnham Black but were in lower numbers at Marengo Reef. There were low abundances of rock lobster Jasus edwardsii at Barnham Black. The nudibranch Tambja verconis made a surprise appearance at this site. This species has been observed rarely during subtidal surveys in other locations. There were relatively low numbers of invertebrates and no numerically dominant species at Merri (Site 3701). Blacklip abalone H. rubra and the periwinkle T. undulatus were the most common species but were present here in very low abundances. There were few other species of mollusc, echinoderm or crustacean each of which was present in low numbers (mostly single individuals). In contrast, the Merri reference site, Breakwater (Site 3702), had relatively high numbers of H. rubra and T. undulatus. Greenlip abalone H. laevigata were recorded in relatively low numbers at this site. Other species common to both the Merri sites included the predatory gastropod molluscs Dicathais orbita and Pleuroploca australasia and the sea urchins Holopneustes porosissimus and Heliocidaris erythrogramma.

31



Table 4.2 Abundance of megafaunal invertebrates and cryptic fishes (200 m-2) at sites on the west coast of Victoria, December 2003-January 2004. Species

Site 3701

3702

3905

3906

3907

3908

3909

3910

3911

3912

Invertebrates 3

Jasus edwardsii

2 1

Strigopagurus strigimanus 1

Hermit u/i Plagusia chabrus

1

4

1

Haliotis rubra

3

62

100

12

4

63

12

Haliotis laevigata

1 41

5

7

1

9

122

1

1

Cabestana spengleri

347

4

5

2

4

Pleuroploca australasia

1

1

2

1

Penion mandarinus

1

1

8

43

140

3

14

1

1

1

1

3

28

21

1

1

3

13

2

1

2

Dicathais orbita

4 1

Scutus antipodes Turbo undulatus

1

17

1

1

Conus anemone 8

Sagaminopteron ornatum

2 1

Tambja verconis C. tasmaniensis

1

Octopus maorum

1

Cenolia trichoptera

1

6

5

1

1 2

Pentagonaster dubeni Nectria ocellata

6

Nectria macrobranchia

1

4

26

4

4

7

2

45

13

9

5

Tosia australis

2

1

4

1

1

9

1

10

1 1

1 2

1

Petricia vernicina 1

Fromia polypora Plectaster decanus

1

5

Cenolia tasmaniae

1

1

Echinaster arcystatus

1

1

Nepanthia troughtoni

1

4

1 4

3

1

Patiriella brevispina 1

Coscinasterias muricata Holopneustes porosissimus

1

2

2

Heliocidaris erythrogramma

3

2

5

1 3

Cryptic Fishes 1

Parascyllium variolatum

1 1

Aetapcus maculatus Bovichtus angustifrons

2

Heteroclinus johnstoni

1

Unidentified heteroclinid

1

1 1 1

Unidentified fish

32



4.3 Population Abundances and Sizes The herbivorous gastropod molluscs Haliotis rubra and Turbo undulatus were the most abundant invertebrates recorded during the surveys (Figure 4.2). Highest abundances of H. rubra were at The Olives (Site 3905; 100 per 200 m-2) and Barnham Black (Site 3912; 140 per 200 m-2). Highest numbers of T. undulatus were at Ingoldsby Inside (Site 3906; 122 per 200 m-2) and Eagle Rock Inside (Site 3909; 347 per 200 m-2-). At sites where H. rubra and T. undulatus were common, one of these species tended to be much more abundant than the other (with the exception of Breakwater (3702) and Marengo Reef (3911)). Sites with low abundances of these molluscs tended to have low overall abundances of invertebrates (Table 4.2). Dicathais orbita occurred at all sites in relatively low to moderate abundance. Most other species of invertebrates occurred in low abundances (generally below 5 individuals per 200 m-2) except for Patiriella brevispina and Cenolia trichoptera which occurred in moderate numbers at Barnham Black (Site 3912). Heliocidaris erythrogramma which can occur in very high numbers at some sites along the Victorian coast were generally low in abundance at the western coast monitoring sites (Table 4.2). Blacklip abalone H. rubra were in sufficient numbers at two sites to allow some assessment of abalone population size structure. Abalone size was roughly normally distributed at The Olives (3905) and at Barnham Black (3912; Figure 4.3). At The Olives in Point Addis MNP, mean abalone size was 107 mm. At Barnham Black (3912), the Marengo reference site, mean abalone size was slightly higher at 112 mm.

Haliotis rubra

400

Individuals per 200 m

2

150

Turbo undulatus

300 100 200 50 100

0

0 01 02 05 06 07 08 09 10 11 12 37 37 39 39 39 39 39 39 39 39

01 02 05 06 07 08 09 10 11 12 37 37 39 39 39 39 39 39 39 39

Site

Site

Figure 4.2 Abundance of common invertebrates on subtidal reefs on the west coast of Victoria

33


20

3905 The Olives

Mean = 107 N = 82

Frequency

15


20

15

10

10

5

5

0

0 0

50 100 Length (mm)

150 0

3912 Barnham Black

Mean = 112 N = 109

50 100 Length (mm)

Figure 4.3 Size frequency distributions for Haliotis rubra at monitoring sites on the west coast of Victoria.

34

150



5.0 FISH 5.1 Species Richness and Diversity Fish species richness varied between 9 and 17 species across all sites but was generally between 12 and 14 species (Table 5.2). Lowest species richness occurred at the Merri sites (Sites 3701 and 3702) with nine species. Highest species richness occurred at Marengo Reef (Site 3911). Similar to the patterns described for species richness, fish species diversity was also relatively even across the monitoring sites (Table 5.1). Highest species diversity occurred at the Marengo Reef sites, both of which had relatively high numbers of species present in relatively low densities (including some species not detected at other western coast sites). Low species diversity was recorded at Eagle Rock Inside (Site 3909), however, this value was influenced by a single school of approximately 100 small (2.5 cm long) unidentified fish (Table 5.2). Table 5.1 Fish species richness and diversity on the west coast of Victoria. Site

Individuals

Species

Heterogeneity

Evenness

N

S

1/D=N2

E1/D

Merri

83

9

4.83

0.54

Breakwater

62

9

4.13

0.46

The Olives

75

12

4.95

0.41

Ingoldsby Inside

180

14

5.50

0.39

Anglesea Reef

30

12

5.77

0.48

Phyco’s Reef

90

13

3.89

0.30

Eagle Rock Inside

142

12

1.96

0.16

Eagle Rock Outside

72

14

5.48

0.39

Marengo Reef

60

17

8.29

0.49

Barnham Black

106

14

6.04

0.43

5.2 Community Structure The MDS representation of fish community structure showed some grouping of sites associated with each marine protected area (Figure 5.1). However, these affinities were not always clear which indicated that there are also substantial differences between assemblages at all monitoring sites. The Point Addis monitoring sites grouped loosely together on the left-hand side of the MDS plot (Figure 5.1). These sites had species in common that were not consistently present at other west coast monitoring sites. These species were scalyfin Parma victoriae, senator wrasse Pictilabrus laticlavius and horseshoe leatherjacket Meuschenia hippocrepis. Blue throat wrasse Notolabrus tetricus was in low to moderate numbers at each of these sites with 35



highest numbers (41 individuals in 2000 m2) at Phyco’s Reef (3908). Herring cale Odax cyanomeles was also present at all the Point Addis sites, in relatively low numbers. Differences between these monitoring sites occurred largely because of low numbers of individuals of different species occurring at each of the different sites. Examples include a single record of Cheilodactylus spectabilis at The Olives (3905), Meuschenia freycineti at Ingoldsby Inside (3906), Dactylophora nigricans at Anglesea Reef (3907) and two records of purple wrasse Notolabrus fucicola at Phyco’s Reef (3908). A school of Pseudocaranx dentex was detected at Ingoldsby Inside (3906). There were relatively few fish at Anglesea Reef (3907). The Eagle Rock sites (Sites 3909 and 3910) were in the centre and upper sections of the MDS plot (Figure 5.1). The most consistently abundant species at these sites were blue throat wrasse N. tetricus, herring cale O. cyanomeles, horseshoe leatherjacket M. hippocrepis and, to a lesser extent, magpie morwong Cheilodactylus nigripes. Scalyfin P. victoriae and yellow-tail leatherjacket M. flavolineata were observed at Eagle Rock Inside (3909) in low to moderate numbers (5 and 7 individuals respectively). There was also a small nest of three Port Jackson sharks Heterodontus portjacksoni resting on sand behind a large isolated bommie at Eagle Rock Inside (3909). Five species of leatherjacket were recorded from Eagle Rock Outside (3910). In contrast to all other west coast monitoring sites, purple wrasse Notolabrus fucicola was the numerically dominant species at the Marengo Reef sites (Sites 3911 and 3912). Blue throat wrasse N. tetricus also occurred but in lower numbers than at all other sites. Herring cale O. cyanomeles was an important species at Barnham Black (3912) and also occurred at Marengo Reef (3911) but in much lower densities. Magpie morwong C. nigripes also occurred in moderate numbers at Barnham Black and in lower numbers at Marengo Reef and Shaw’s cowfish Aracana aurita occurred at these two sites exclusively. Blue throat wrasse N. tetricus was the most abundant fish at the Merri sites (Sites 3701 and 3702). Other fish common to both these sites included purple wrasse N. fucicola, herring cale O. cyanomeles, southern sea carp Aplodactylus arctidens and magpie morwong C. nigripes. Each of these species was in moderate to low abundance. Five long finned pike Dinolestes lewini and several sea sweep were observed higher in the water column at Merri (3701). There were several zebra fish Girella zebra recorded at Breakwater (3702).

36



3909 3907

3911

3910 3908 3702

3912

3905

3701

3906

Figure 5.1 MDS plot of fish assemblage structure on the west coast of Victoria, December 2003January 2004. The labels next to each point denote the survey site. Kruskall stress = 0.13

37



Table 5.2 Fish abundance (2000 m-2) at monitoring sites on the west coast of Victoria, December 2003-January 2004. Species

Site 3701

3702

3905

3906

3907

3908

Heterodontus portusjacksoni

3910

3911

3912

2

3

3 3

Parascyllium variolatum 1

Dasyatis brevicaudata 30

T. caudimaculatus Dinolestes lewini

3909

5

1

16

1 60

Pseudocaranx dentex Upeneichthys vlaminghii

1

5

2

1

2

Pempheris multiradiata

1

Girella tricuspidata Girella zebra

1

8

3

15

Scorpis aequipinnis

21

1

9

13

4

18

4

Scorpis lineolata

1 2

Atypichthys strigatus 2

Tilodon sexfasciatus 1

Enoplosus armatus Parma victoriae

7

Aplodactylus arctidens

3

Cheilodactylus nigripes

4

11

15

2

3

1

2

2

1

1

3 6

1

1 1

1

2

3

5

1

Cheilodactylus spectabilis

1

Dactylophora nigricans

2 1

Latridopsis forsteri

1

Achoerodus gouldii 1

Dotalabrus aurantiacus Notolabrus tetricus

28

24

Notolabrus fucicola

8

7

1 29

26

10

1

2

1

41

10

25

8

6

2

1

3

16

22

6

3

13

4

1

Pseudolabrus psittaculus Pictilabrus laticlavius Odax cyanomelas

6

15

3

3

5

3

3

1

1

3

12

1

Acanthaluteres vittiger 6

8

1

7

1

1

Meuschenia freycineti

1 3

2

7

4

5

1

1 5

6

Aracana aurita Diodon nichthemerus

3

1

Meuschenia galii Meuschenia hippocrepis

28

1

Haletta semifasciata Meuschenia flavolineata

13

3

6

2

1

4 100

Unidentified fish

38

1

2



5.3 Population Structure Some fish were detected in relatively high numbers during west coast surveys and so an assessment of the population size structure was possible. Blue throat wrasse Notolabrus tetricus was generally the most abundant species at all sites along the western coast of Victoria. This is generally consistent with many other locations along the open Victorian coast. The sex ratio of N. tetricus was heavily biased towards females which is typical for this species (Table 5.3). There was some variation between sites; longer term information from ongoing monitoring will allow more detailed analysis of sex ratio in these populations. Sizes of fish were mostly between 20 and 30 cm. Larger size classes between 40 and 50 cm were predominantly male individuals. There were relatively few small fish below 12.5 cm during this survey (Table 5.3) There were relatively low densities of purple wrasse Notolabrus fucicola at all sites. The population size structure of N. fucicola was similar to that of N. tetricus with most fish being between 20 and 30 cm long (Table 5.4). Herring cale Odax cyanomeles occurred at all sites but in variable abundance. Most fish were between 30 and 37.5 cm long. There were insufficient individuals to accurately assess sex ratio in this species (Table 5.5).

Table 5.3 Population structure of blue throated wrasse Notolabrus tetricus on the west coast of Victoria Site

% male

Length (mm) n

mean

sd

Length Class (mm) 75

100

125

150

200

250

300

350

375

3

2

4

5

4

3

3

2

400

500

3701

7

28

167

97

3702

21

24

220

104

2

4

6

3

1

2

3

1

3905

14

29

221

90

1

3

9

3

6

2

2

1

3906

4

26

147

76

4

2

9

4

3907

10

10

180

80

1

1

5

3908

15

41

223

106

3

2

6

14

4

10

180

66

2

2

3

3

3

4

8

3

2

2

3909 3910

22

25

233

88

3911

13

8

181

115

3912

17

6

221

124

2

3

1

2

1

3

39

1 2

1 3

2

1

4 1

1

1

1

1



Table 5.4 Population structure of purple wrasse Notolabrus fucicola on the west coast of Victoria Site

% male

Length (mm) n

mean

sd

3701

8

178

67

3702

7

171

62

3908

2

175

35

3909

1

200

3910

3

250

50

3911

16

222

82

3912

22

197

59

Length Class (mm) 75

100

125

150

200

250

300

350

375

1

1

3

1

1

1

2

3

1

1

1

400

500

1

1 1 5

1

1

1

4

5

2

2

4

5

6

2

1

Table 5.5 Population structure of herring cale Odax cyanomelas on the west coast of Victoria Site

% male

Length (mm) n

mean

sd

3701

33

6

275

82

3702

7

15

232

82

3905

67

3

250

100

3906

1

125

3907

1

250

3

317

58

3909

17

12

248

76

3910

15

13

308

76

4

313

75

28

272

90

4

100

125

150

200

250

300

1 1

2

7

1

350

375

2

2

1

1

1

400

2 1

1

33

3912

75

1

3908

3911

Length Class (mm)

1 1

2

3

4

2

2

3

1

3

3

2 1

40

1

1

6

5

1 5

5

500



6.0 REFERENCES Clarke K. R. (1993) Non-parametric multivariate analyses of changes in community structure. Australian Journal of Ecology 18: 117-143. Dayton P. K., Tegner M. J., Edwards P. B. and Riser K. L. (1998) Sliding baselines, ghosts, and reduced expectations in kelp forest communities. Ecological Applications 8: 309-322. Ebeling A. W., Laur D. R. and Rowley R. J. (1985) Severe storm disturbances and reversal of community structure in a southern California kelp forest. Marine Biology 84: 287-294. Edgar G. J. (1998) Impact on and recovery of subtidal reefs. In: Iron Barron Oil Spill, July 1995: Long Term Environmental Impact and Recovery. Tasmanian Department of Primary Industries and Environment, Hobart, pp273-293. Edgar G. J., Barrett N. S. (1997) Short term monitoring of biotic change in Tasmanian marine reserves. Journal of Experimental Marine Biology and Ecology 213: 261-279. Edgar G. J. and Barrett N. S. (1999) Effects of the declaration of marine reserves on Tasmanian reef fishes, invertebrates and plants. Journal of Experimental Marine Biology and Ecology 242: 107-144. Edgar G. J., Moverly J., Barrett N. S., Peters D., and Reed C. (1997) The conservationrelated benefits of a systematic marine biological sampling program: the Tasmanian reef bioregionalisation as a case study. Biological Conservation 79: 227-240. Edmunds M. and Hart S. (2003) Parks Victoria Standard Operating Procedure: Biological Monitoring of Subtidal Reefs. Parks Victoria Technical Series No. 9, Parks Victoria, Melbourne. Edmunds M., Hart S., Jenkins S. and Elias J. (2003) Victorian Subtidal Reef Monitoring Program – The reef biota at Wilsons Promontory Marine National Park. Parks Victoria Technical Series No. 6, Parks Victoria, Melbourne. Edmunds E, Roob R. and Ferns L. (2000) Marine Biogeography of the Central Victoria and Flinders Bioregions – a Preliminary Analysis of Reef Flora and Fauna. In: L. W. Ferns and D. Hough (eds). Environmental Inventory of Victoria’s Marine Ecosystems Stage 3 (Volume 2). Parks, Flora and Fauna Division, Department of Natural Resources and Environment, East Melbourne. Australia. Faith D., Minchin P. and Belbin L. (1987) Compositional dissimilarity as a robust measure of ecological distance. Vegetation 69: 57-68.

41



Holling C. S. (1978) Adaptive Environmental Assessment and Management. Wiley, Chichester. Krebs C. J. (1999) Ecological Methodology, Second Edition. Benjamin/Cummings, Menlo Park. Meredith C. (1997) Best Practice in Performance Reporting in Natural Resource Management. Department of Natural Resources and Environment, Melbourne. Roob R., Edmunds M. and Ball D. (2000) Victorian Oil Spill Response Atlas: Biological resources. Macroalgal Communities in Central Victoria. Unpublished report to Australian Marine Safety Authority, Australian Marine Ecology Report No. 19, Melbourne. Sweatman H., Cheal A., Coleman G., Fitzpatrick B., Miller I., Ninio R., Osborne K., Page C., Ryan D., Thompson A. and Tomkins P. (2000) Long-term Monitoring of the Great Barrier Reef. Status Report Number 4. Australian Institute of Marine Science, Townsville.

42



7.0 ACKNOWLEDGEMENTS This project was funded by Parks Victoria and supervised by Dr Anthony Boxshall. We are grateful for the field assistance of Jeff Giddins of Scuttlebut Scuba.

43

Parks Victoria is responsible for managing the Victorian protected area network, which ranges from wilderness areas to metropolitan parks and includes both marine and terrestrial components. Our role is to protect the natural and cultural values of the parks and other assets we manage, while providing a great range of outdoor opportunities for all Victorians and visitors. A broad range of environmental research and monitoring activities supported by Parks Victoria provides information to enhance park management decisions. This Technical Series highlights some of the environmental research and monitoring activities done within Victoria’s protected area network. Healthy Parks Healthy People

For more information contact the Parks Victoria Information Centre on 13 1963, or visit www.parkweb.vic.gov.au

Victorian Subtidal Reef Monitoring Program - Parks Victoria

Victorian Subtidal Reef Monitoring Program - Parks Victoria

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