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BELIZE MARINE CONSERVATION AND

DIVING PROGRAMME

Caye Caulker, Belize

BZM Phase 144 Science Report

September - December 2014

Clio Maggi (Principal Investigator), Sophie Burns (Research Officer) &

Robyn Samuel (Assistant Research Officer)

Staff Members

Name Position

Clio Maggi (CM) Principal Investigator (PI)

Sophie Burns (SB) Research Officer (RO)

Robyn Samuel (RS) Assistant Research Officer (ARO)

Contents

1.0 Introduction............................................................................................................................. 5

1.1 Project Background and Location ....................................................................................... 5

1.2 Aims of the Project .............................................................................................................. 7

1.3 Phase 144 Achievements ..................................................................................................... 8

2.0 Field Training ........................................................................................................................... 8

2.1. Science Training and Volunteer Briefings ......................................................................... 8

2.2 Dive Training ...................................................................................................................... 9

2.3 BTEC................................................................................................................................. 10

3.0 SMP Benthic, Fish & Invertebrate Surveys ............................................................................ 10

3.1 Introduction ....................................................................................................................... 10

3.2 Survey Sites ....................................................................................................................... 11

3.3 Methodology ..................................................................................................................... 12

3.4 Results and Discussion ...................................................................................................... 13

3.4.1. Physical surveys: Coral colony characterization ........................................................ 13

3.4.2 Fish surveys ................................................................................................................ 14

3.4.3. Benthic surveys ......................................................................................................... 16

4.0 Queen Conch Surveys ....................................................................................................... 17

4.1 Introduction ....................................................................................................................... 17

4.2 Methodology ...................................................................................................................... 19


5.0 Caribbean Spiny Lobster Surveys .......................................................................................... 22

5.1 Introduction ....................................................................................................................... 22

5.2 Methodology ..................................................................................................................... 23


6.0 Seagrass Monitoring .............................................................................................................. 24

6.1Introduction ........................................................................................................................ 24

6.2 Aims and Objectives ......................................................................................................... 25

6.3 Methodology ..................................................................................................................... 25

7.0 Mangrove Monitoring ........................................................................................................... 26

6.1 Introduction ....................................................................................................................... 26


6.3 Methodology ..................................................................................................................... 26

8.0 Marine Debris Monitoring ..................................................................................................... 27

8.1Introduction ........................................................................................................................ 27


8.3 Methodology ..................................................................................................................... 28

9.0 Community Work and Public Awareness .............................................................................. 28

10.0 References ........................................................................................................................... 31

11.0 Appendices .......................................................................................................................... 36

11.1 Appendix 1 ...................................................................................................................... 36

11.2 Appendix ......................................................................................................................... 41

11.3 Appendix ......................................................................................................................... 42

11.4 Appendix ......................................................................................................................... 43

11.5 Appendix ......................................................................................................................... 43

11.6 Appendix ......................................................................................................................... 43

1.0 Introduction

1.1 Project Background and Location

The Frontier Belize Marine Conservation and Diving (BZM) Project was established in April

2014 within the Caye Caulker Forest and Marine Reserve. The Frontier Belize camp hosts

Marine Conserv

0 W ast of Belize in the

Caribbean Sea (Figure 1).

Figure 1. Location of Frontier Belize Marine Conservation base camp on the north island of Caye

Caulker (marked in red).

The project aims to conduct long term monitoring of key habitats and species, using

international volunteers as a workforce, and to work in collaboration with the Fisheries

Department of Belize (FD) and the Forest and Marine Reserve Association of Caye Caulker

(FAMRACC), the two local organisations that currently co-manage the reserve.

Belize is a small, tropical, Caribbean country, located at the northeast end of Central America,

bordering Mexico to the north and Guatemala to the west and south. The country has one of the

most extensive and diverse reef ecosystems in the Western hemisphere, including the second

largest barrier reef in the world, three atolls and a complex network of inshore patch reefs and

fringing reefs (Gibson et al, 1998).

Caye Caulker is a small limestone coral island, approximately five miles from north to south

and less than one mile east to west at its widest part. A very narrow waterway, referred to as the

'split’, separates the island in two. The population of Caye Caulker is approximately 1500, with

the much smaller south island holding the majority of residents. The island lies just 21 miles

east of the mainland and is a busy tourist destination; this is mostly due to its abundant marine

flora and fauna, which provide excellent snorkeling and diving opportunities. As with much of

our natural world local marine life is under threat and includes species of international concern:

staghorn and elkhorn corals (Acropora cervicornis and A. palmata), and hawksbill turtle

(Eretmochelys imbricata), ‘ green (Chelonia mydas) and

loggerhead (Caretta caretta) turtles ‘ ( U 20 ). The marine reserve is

also home to West Indian manatees (Trichechus manatus) ‘vulnerable , and

common bottlenose dolphins (Tursiops aduncus), ‘ b

species is understudied and threatened by many anthropogenic(Belize Fisheries Department,

2010; IUCN, 2014). In addition to this, the reserve, and Belize in general, also provide

residence for two of the most commercially important invertebrate species in the Caribbean; the

Caribbean spiny lobster (Panulirus argus) and the queen conch (Strombus gigas). Currently

there is a strict management regime regarding the harvesting of these species which includes

regulated fishing seasons for each species and size and gear restrictions, in order to maintain

healthy and sustainable populations within the area. Size is a useful parameter to control and

manage the overfishing of conch or lobster populations since the shell of the queen conch and

the carapace of the spiny lobster provide an important function for estimating sexual maturity

(Huitric, 2005).

The Caye Caulker Marine Reserve (CCMR) is part of the 9,000 acre Mesoamerican Barrier

Reef System (MBRS), which runs parallel to the entire caye and it is11km long, extending to

the Belize barrier reef from the northern tip of Caye Caulker. The CCMR was established in the

early 1990s but did not become completely recognized as a marine reserve until 1998, at which

point it was included alongside the Caye Caulker Forest Reserve (CCFR), as part of a single

management unit. This unit was set up with the aim of ensuring protection of the littoral forest,

reef lagoon, reef crest and fore reef areas. Today, both reserves are co-managed by FAMRACC

and the FD.

This management unit encompasses five habitats; mangrove and littoral forests, lagoon marsh-

lands, seagrass beds and coral reefs. The marine reserve is managed through the use of three

regulated zones allowing differing levels of use and protection; the General Use Zone, the

Conservation Zone and the Preservation Zone. The General Use Zone comprises 6,199 acres,

the Conservation Zone 2,029 acres, and the Preservation Zone 1,442 acres (Belize Fisheries

Department, 2010). Both the Conservation and Preservation Zones are non-extractive and do

not allow fishing, however the Conservation Zone allows for recreational use, which primarily

includes snorkeling and diving. The Preservation Zone does not allow recreational use and is

principally set aside for the recovery of overexploited populations of marine life. The General

Use Zone permits commercial and sports fishing alongside other recreational use, such as

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it generates through tourism: residents of Caye Caulker are mostly dependent upon tourism as a

source of income. The reserve also provides essential environmental services, through helping

maintain local populations of important commercial species and the overall health of the reef,

whilst at the same time protecting Caye Caulker from storm damage and erosive influences

(Belize Fisheries Department, 2010). Consequently, research into the sustainability and

effectiveness m ment plan is essential for stakeholders involved,

and is something that is relatively understudied. Management of the Belize barrier reef was

originally envisioned through the creation of marine protected areas, however, the influence of

land-based activities was not accounted for within these programs. As a result the focus was

shifted towards the previously described integrated, multi-sectoral approach currently used in

Belize's marine reserves (Cho, 2005), including Caye Caulker Marine Reserve.

The research conducted by Frontier within the CCMR lies within the MBRS and therefore

involves methods adapted from the MBRS Regional Synoptic Monitoring Program (SMP), a

multi-level methodology designed to monitor changes in ecosystem health for research and

management purposes. Standard Frontier methodology is also incorporated to provide an

effective and yet reliable way of utilizing volunteers as a resource for data collection during

surveys. With the described volunteer workforce, Frontier aims to assist the Fisheries

Department and FAMRACC with data collection and analysis, survey techniques, marine and

forest reserve maintenance and community education and awareness through the projects

discussed below.

1.2 Aims of the Project

1. Establish fixed survey sites in addition to the sites currently used by the FD and FAMRACC

for each survey type. From this, formulate a schedule on the frequency of visits required per

phase at each location. The establishment of fixed survey sites will allow the monitoring of

changes over time and for extended data collection within the reserve from areas with different

management levels, therefore providing insight into the effect of anthropogenic impacts,

particularly fishing, and thereby assessing the effectiveness of the marine reserve and its multi-

sectored structure.

2. Collect baseline data on the health of the coral reefs, water quality and the various key fish

and invertebrate species associated with such ecosystems around the Caye Caulker MBRS,

using modified methods used by the FD and FAMRACC. This will supplement the existing

long term, but currently limited, ongoing data collection and contribute to the collection of

pollution data under the MBRS SMP.

3. Collect data on commercially important invertebrate species including the queen conch and

the Caribbean spiny lobster consistently throughout the year to expand on the current biannual

data collection, during open and closed fishing season, using tailored methods used by the FD

and FAMRACC.

4. Initiate a seagrass project comprised of seagrass mapping and species composition analysis

within the 'home' sea grass meadows by camp and in the future potentially extend this to include

long term monitoring which requires sample analysis and the use of more specialised

equipment.

5. Initiate a mangrove restoration project within the forest reserve and use this to assess the

feasibility of devising a methodology to provide regular data collection and long term

monitoring on the mangrove habitat and implement more terrestrially focused surveys.

6. Instigate and build on solid local relations necessary for developing an education project

within the town of Caye Caulker and organizing regular environmental awareness days and

activities.

7. Continue with the recording of any opportunistic manatee sightings during training dives and

potentially use this data in the future to map the local manatee population.

8. Continue to add further protocols outlined in the research proposal (Owen, 2013) including

habitat mapping, terrestrial species surveys and performing Rapid Assessments within one week

of the disturbance.

1.3 Phase 144 Achievements

1. The SMP, fish and benthic surveys have continued during this phase, with three out of the

four sites (previously defined by the Caye Caulker Fisheries department) being surveyed

regularly. For the next phase, regular surveys to the fourth site will take place and additional

sites will be established to increase survey area and to decrease the frequency of visits per site

and thus decrease the level of any human disturbance created.

2. Seven queen conch surveys have now been completed across the differently managed zones

within Caye Caulker Marine Reserve, this project will continue with the bimonthly conch

surveys during the next phase at the three established sites, every other week, on a rotation

basis.

3. Seven Caribbean Spiny Lobster surveys have been conducted at each of the two defined sites

that were previously established by the Caye Caulker Fisheries Department. During the next

phase of the project these surveys will continue with their bi-monthly schedule, rotating

between each site surveyed every two weeks.

4. For the seagrass monitoring project, methodology development and preliminary surveys have

been conducted during a four week BTEC. During the next phase of the project, regular

conduction of these surveys will be initiated after the establishment of permanent sites for these

surveys that do not require the use of a boat for access.

5. Methodologies for mangrove habitat monitoring have been finalised during this phase and

will be implemented at the start of the next phase with the first beach conservation RAs. This

will include species identification and distribution, assessment of mangrove health, and an

evaluation of the success of the mangrove restoration programme which was initiated by

FAMRACC.

6. One beach cleanup involving school children has been organised in collaboration with

FAMRACC. Involvement with the school will continue during the next phase, including an

Environmental Awareness Day.

7. Opportunistic manatee and cetacean sightings have been recorded during this phase. During

the next phase there is a plan to involve local dive and snorkel shops as well as local fishermen

in the recording of opportunistic sightings in order to gain an understanding of their populations

at a wider spatial scale and on a more frequent basis.

2.0 Field Training

2.1. Science Training and Volunteer Briefings

To achieve the above aims, all volunteers and staff members receive a combination of briefings,

science presentations and lectures and practical field training (Table 1) before conducting any

marine surveys. For all tests a 95% pass mark is required and in case of any failures, multiple

tests have been produced. All marine conservation and diving volunteers are also PADI scuba

trained to at least Advanced Open Water level.

Table 1. Science Lectures, Field Training Lectures and Tests and Briefings.

Lecture/Presentation/Test Lecturer

Health and safety and medical presentations

and tests

SB, CM

Dangers of the reef presentation SB, CM, RS

Introductory science presentation for Frontier

Belize Project

SB, CM, RS

Introduction to Coral Reefs Presentation SB, CM, RS

Benthic identification and survey methodology

presentation

SB, CM, RS

Coral health presentation SB, CM, RS

Coral flash, revision slides SB,CM, RS or independently

Benthic test SB, CM, RS

In water, practical benthic test SB, CM, RS

Fish identification presentation SB, CM, RS

Fish flash, revision slides SB, CM, RS or independently

Fish families test SB, CM, RS

Fish ID test SB, CM, RS

Juveniles and recruits fish ID test SB, CM, RS

In water, practical fish test SB, CM, RS

Practice mock survey SB, CM, RS

Queen Conch Presentation SB, CM, RS

Caribbean Spiny Lobster Presentation SB, CM, RS

Mangrove Presentation RS

Seagrass Presentation RS

Beach Clean Presentation RS

Invertebrate Presentation RS

Invertebrate Test RS

2.2 Dive Training

All volunteers are trained up to at least PADI Open Water Advanced. PADI dive training is

currently being outsourced to a local dive company, 'Frenchies Diving Services' and this will

continue until Fro b ‘ -

2.3 BTEC

No BTECs were conducted during this phase (Table 2).

Table.2 BTEC projects conducted during BZM144

Name BTEC Project Duration

N/A N/A N/A

3.0 SMP Benthic, Fish & Invertebrate Surveys

3.1 Introduction

Coral reefs are often argued to be one of world's mostly heavily impacted marine ecosystems,

with the most widely accepted causes being overfishing, increased ocean temperatures, coral

disease and predator outbreaks and poor land-use practices. As a result reef ecology is altered,

sedimentation and nutrient pollution occurs as well as direct and indirect impacts that result

from climate change and human activities (Schutte et al, 2010). Coral reefs are among the most

threatened global ecosystems, as well as the most vital, contributing to human survival,

especially in developing countries (Bryant et al, 1998; Costanza et al, 2007).

Caribbean coral reefs have experienced numerous, recent ecological changes, which are

frequently associated with the death of corals through disease, bleaching and other

environmental and anthropogenic disturbances. The region was also rampaged by hurricanes in

2000, 2001 and 2002, destroying many coral formations with recorded losses of up 75% in

Belize (Almada-Villela et al, 2002); additionally these impacts all followed closely after

Hurricane Mitch and an extreme bleaching event in 1998. A region-wide survey found evidence

suggesting that three years after the event, coral cover had still not increased in many of the

areas affected (Mumby, 1999). Many observations of widespread bleaching within reefs of the

tropics were documented in summer and autumn of 1998, resulting from unprecedented

elevations in sea surface temperatures due primarily to a severe El Nino Southern oscillation

and possibly augmented by global warming (Goreau et al, 2001). Corals in all habitats along the

Belizean area of the Mesoamerican Barrier Reef bleached as a result of these thermal anomalies

(Mumby, 1999). By 1999, some fore-reef habitats demonstrated signs of recovery; in contrast,

coral populations amongst the sheltered lagoons of the back reef still displayed reduced coral

cover, low coral recruitment and little indication of recovery. Aronson et al (2002) determined

that during this prolonged period of elevated sea surface temperatures, anomalies peaked at

4.0°C above the local hotspot threshold, which is an extraordinary increase compared to

previous years' sea surface temperatures.

Traditionally, coastal and marine activities in the area have been relatively minor, however, this

is changing with a rapidly growing tourism industry, especially increases in the number of

cruise ships, particularly in Caye Caulker (Almada-Villela et al, 2002). Increases in activity

have resulted in increased algal cover dominating the reefs (McClanahan et al, 2001) and

therefore a decline in coral cover, especially in the Caribbean (Schutte et al, 2010). This is

concerning as fish assemblage is often directly associated with coral reef health. Promisingly,

Belize boasts the highest fish diversity in the MBRS region, with over 320 recognised fish

species, but with fishing in the region intensifying this diversity is under threat. This presents

threats particularly towards spawning aggregations, as spawning location depends on the

recognisable characteristics of cayes and reefs, something which may be lost with overfishing.

A documented example of this is the Nassau grouper (Epinephalus striatus) which forms

spawning aggregations annually in the same location, during the full moons of December and

January, allowing fishermen to become very familiar with these cycles. This species is currently

on the IUCN Red List of Threatened Animals and is now seldom observed within the reefs of

Caye Caulker Marine Reserve (Almada-Villela et al, 2002), despite its protected status in

Belize. Worryingly, a study conducted by Hughes et al (2007) established that the exclusion of

large predatory and herbivorous fish led to a dramatic explosion of macro-algae, suppressing the

fecundity, recruitment and survival of coral, ultimately reducing total coral cover within reef

systems. Consequently, the coordination and control of fish stocks is one of the primary

components in preventing phase shifts and managing reef resilience.

Disturbances to the invertebrate community have also profoundly influenced reef health in the

area; disease has dramatically reduced populations of the herbivorous sea urchin Diadema

antillarum, contributing to the increased abundance of macro-algae and reduced coral cover

(Harbone et al, 2009). Many other macro-invertebrate species also play an important role in

reducing macro algae cover, by grazing on the biofilms on substrate suitable for hard coral

cover (Klumpp & Pulfrich, 1989). Furthermore, it is important to monitor the abundance and

diversity of macro-invertebrates such as the commercially important Queen Conch (Strombus

gigas), the Spiny Lobster (Panulirus argus) and the Donkey Dung Sea Cucumber (Holothuria

mexicana), which are prone to overfishing (Theile, 2002; Pollock, 1993; Perez & Garcia, 2012).

The Mesoamerican Barrier Reef System (MBRS) is approximately 1000 km long and extends

through Mexico, Belize, Guatemala and Honduras. This system includes the largest, continuous

barrier reef in the Western Hemisphere, the Belize Barrier Reef Complex; a 250 km long reef

running parallel to the coast of Belize. The MBRS project was designed and implemented to

improve the protection of this vulnerable marine ecosystem and to promote sustainable

utilisation of its resources (Gomez, 2004). This is of particular importance in Belize since the

fishing industry is the third largest foreign exchange income, meaning the country is heavily

dependent on the health and productivity of the reef (Belize Fisheries department, 2007).

Fishing within Caribbean reefs such as Belize has been occurring long before the arrival of

European settlers in the 16th century, but over the last 200 years, as human populations in the

area have escalated, the yields being returned are diminishing progressively (Stallings, 2009).

With the establishment of the MBRS Synoptic Monitoring Program (SMP), the MBRS Protocol

was designed to standardise data collection and management for ecosystem monitoring. It aims

to monitor changes in ecosystem health within priority protected areas, enabling quicker and

more effective responses to changes in reef health (Gomez, 2004). Ultimately the utilisation of

this protocol and the work conducted by Frontier will provide much needed comparable

baseline data on the state and associations of marine ecosystems through continuous long-term

monitoring.

3.2 Survey Sites

Site 1; North Back-reef: (16Q 0393822 UTM 1966284) A shallow patch reef on the inside of

the MBRS which is located between the reef crest and a lagoon, with a maximum depth of

approximately 5m and within the General Use Zone of CCMR. Current flow and wave energy

are generally moderate to high on days with greater wind force.

Site 2; North Fore-reef: (16Q 0394839 UTM 1966980) A barrier reef on the inside of the

MBRS with a maximum depth of approximately 15m in the General Use Zone of CCMR. This

site is only accessible on moderately calm days, when the wind force and sea state is relatively

low.

Site 3; South Back-reef: (16Q 0392922 UTM 1959724) A shallow patch reef on the inside of

the MBRS which is situated between the reef crest and the lagoon, with a maximum depth of

approximately 5m and located in the Conservation Zone of CCMR. This reef is subject to many

regular, touristic activities, including PADI Open Water training and snorkeling tours. Current

flow remains moderately low.

Site 4; South Fore-reef: (16Q 03993628 UTM 193628) A relatively deep reef on the outside of

the MBRS with a maximum depth of approximately 20m in the General Use Zone of CCMR.

This reef is subject to moderate levels of touristic activities, predominantly in the form of PADI

dive training and recreational scuba diving. This site is only accessible on moderately calm

days, when the wind force and sea state is relatively low.

3.3 Methodology

The protocol for this survey has been adopted by the MBRS Synoptic Monitoring Program as

the standard methodology that is used to monitor the coral reefs at established sites (Almada-

Villela et al, 2003). Survey methods have been adapted for the Belize Fisheries Department,

FAMRACC and Frontier. For each survey a minimum of three divers are required and each has

a very specific role for which they have undergone the required training for. In the next project

phase, an additional diver will be required as invertebrate surveys will be included as part of the

SMP surveys.

Diver 1:Physical surveyor: characterization of the coral community below the transect.

For each transect the following information will be recorded; name, date, start and

end time, start and end depth and GPS coordinates for the site. A 30m transect line is laid down

by first placing the weighted (2lbs) end of the line on the sea bottom, at a randomly selected

location within the general confines of the site. Using an underwater compass, the diver swims

parallel to the reef in a straight line, while releasing the tape from the reel until the 30m has

been completed. On the return journey the diver swims back along the transect, stopping at the

first coral colony that is located directly beneath the transect line and is at least 10cm in

diameter. For each colony surveyed the following is recorded; the species of coral, the measured

(to the nearest mm) diameter and maximum height (measure from the base of the substratum) of

the colony. The percentage of recently dead or long dead coral is estimated and recorded along

with the presence of any diseases and/or bleached tissues. The surveyor then moves on to the

next appropriate coral and repeats the above measurements until at least 10 coral colonies are

sampled from each site.

Diver 2: Fish surveyor: belt transect counts for defined fish species list.

The fish surveyor swims alongside the physical surveyor whilst the transect is reeled out, trying

to minimise any changes in depth. Whilst swimming out the full 30m transect line the surveyor

counts and records the defined fish species observed within a 2m wide visually estimated belt

transect (1m either side of the line). The size of each fish recorded is estimated by assigning

them to the following size categories (<5cm, 5-15, 16-30, 31-40, >40cm). A two minute pause

is taken once the surveyor has reached the end of the transect before commencing the survey for

recruits on the return journey (Almada-Villela et al, 2003). On the return journey, the surveyor

swims along the 30m transect recording only selected juvenile fish, fish species <5cm and

Diadema sea urchins. The latter is recorded as part of the fish survey whenever an Invertebrate

Surveyor is not present.

Diver 3:

Benthic Surveyor: point intercept for percentage cover of corals, algae and other sessile

organisms.

The surveyor swims along the 30m transect to approximate the percentage cover of sessile

organisms by recording the organism directly below every 25cm point along the line. The

substrate underneath every 25cm point is recorded even if it is rock, sand or dead coral. This

yields 120 records per 30m transect. On the return journey the surveyor reels the 30m transect

back in and then joins the other two divers at the weighted end of the reel once all parts of the

survey have been completed.

Diver 4:

Invertebrate Surveyor: Belt transect counts for defined invertebrate species.

The surveyor swims along the 30m transect to count and record all defined invertebrate species

within a 2m wide visually estimated belt transect (1m either side of the line). The surveyor

takes time to check under overhangs and inside crevices.

3.4 Results and Discussion

There has not yet been enough data collected between the four sites to allow effective data

analysis. Fifty recordings are needed for the coral colony characterisation aspect of the site to be

completed, therefore each site needs to be surveyed a minimum of five times for all the required

data. To date, only one survey site (North Back-reef) has been surveyed five times and thus has

completed one cycle of data collection. Furthermore, because sites at the fore-reef can only be

surveyed on very calm days, each SMP site has not been surveyed an equal number of times to

allow for any accurately representative comparisons of coral and algal cover amongst the

different sites and what this may suggest about reef health within CCMR. However by

summarizing the data collected so far, it was possible to identify some trends.

3.4.1. Physical surveys: Coral colony characterization

From the limited data available for the coral characterisation surveys some trends in coral

mortality at the different sites can be identified. The mean percentage of dead coral was variable

for the different coral species at the four survey sites. At North Back Reef, mortality was found

to be particularly high for Staghorn coral (ACER – Acropora cervicornis), Lettuce Coral

(AAGA – Agaricia agaricites) and Rose Coral (MARE – Manicina areolata) (Figure 2). In

South Back Reef, on the other hand, a higher percentage of Clubtip finger Coral (PPOR- Porites

porites) and Symmetrical Brain Coral (PSTR-Pseudo-diploria strigosa) were recorded as dead.

The coral colonies at North Fore Reef did not exhibit a high percentage of dead coral, however,

22.5% of Mustard hill coral (PAST- Porites astreoides) and 25% of Clubtip Finger Coral

(PPOR- Porites porites) were dead at this site. There was no available data for South Fore Reef,

as surveys have not yet been conducted at this site.

Figure 2. Mean percentage dead coral for each of the species found at the four SMP sites

3.4.2 Fish surveys

Herbivorous fish found in these reefs include the Parrotfishes and Surgeonfishes. The important

commercial fish in the CCMR are mainly the Grouper and Snapper species (Gibson et al, 1998).

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Figure 3. The average number of fish present in each size category within the four defined

survey sites in CCMR .

The south back reef appears to have more fish in each size category except >40 cm. This

appears to be indicating a successful reserve. However, as the reserve is still relatively new,

being established in 1998, without enforced regulations until 2004 (APAMO, 2015); the lack of

large fish could be a result of the slow recovery rates often seen in larger species, which are

most targeted by fishing practices (Russ & Alcala, 1996).

Figure 4. The Average number of commercially important and herbivorous fish present within

the defied sites of CCMR.

The South back reef appears to have on average far more herbivorous fish (61.00) than both

north fore reef and north back reef (13.33 & 15.43). Having a lot of herbivorous fish is good

the coral health as they keep algal cover low exposing more suitable substrate for hard coral

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cover (Chong-seng et al, 2012) Due to the lack of data on south fore reef and only one survey

at South Back Reef results should be interpreted with caution.

Figure 5. Average number of juveniles present within the four defined survey sites in CCMR.

The most abundant species at North Fore Reef were Striped Parrotfish (Scarus iseri), Bluehead

Wrasse (Thalassoma bifasciatum) and, to a lesser extent, Slippery Dick (Halichoeres bivittatus)

(Figure 4). Striped Parrotfish (Scarus iseri) was also the most abundant species at North Back

Reef. The most abundant species at South Back Reef were Bicolor damselfish (Stegastes

partitus), Striped Parrotfish (Scarus iseri), Princess Parrotfish (Scarus taeniopterus), Stoplight

Parrotfish and Bluehead Wrasse (Thalassoma bifasciatum). Surveys have not yet been

conducted on the South Fore Reef, therefore no data was available for this site. Due to the

limited number of surveys conducted, as well the lack of data for one of the sites, it was not

possible to conduct statistical analysis to compare juvenile fish abundance at the different sites.

3.4.3. Benthic surveys

The species identified by the benthic surveyor were grouped into Hard Corals (HC), suitable

substrate for hard coral growth (SS), Gorgonians (GG), Sponges (SPN), Fleshy Algae suitable

for herbivorous grazing (FA), Critically endangered Elkhorn and Staghorn species (Acropora

sp.) and Fire Corals (Millepora sp.). These groupings were based on a classification method

used by FAMRACC for their surveys.

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North Back

South Back

Figure 6. Average percentage cover of sessile organisms and substrate within the four defined

survey sites in CCMR.

From the limited data available it appears the South Back Reef has more hard coral cover and

less fleshy algae cover. This is likely because the south back reef is within the conservation area

where no fishing is allowed meaning herbivorous species, such as Surgeonfish and Parrotfish,

may be more abundant, reducing the amount of fleshy algae through grazing. Reduced fleshy

algae subsequently allows for greater hard coral growth. Interestingly, in the south back reef

there was no suitable substrate for coral growth this is likely to a good indicator for a healthy

reef, as all suitable substrate has been colonized due to its high percentage of hard coral cover

(40.8%). There has been no data collected for the south fore reef due to the additional costs

involved in collecting data there.

4.0 Queen Conch Surveys

4.1 Introduction

The queen conch is one of the largest gastropods found in the Caribbean (up to 30cm shell

length) and one of the most extensively fished marine invertebrates throughout the region (Chan

et al, 2013). This species is highly economically valuable within Caribbean countries, including

Belize. In particular, queen conch fishing has significantly contributed to Belize's economy,

being recorded as the second largest export from Belize (King and Petruny, 2012). Increasing

fishing pressures caused population declines in the 1980's. As a consequence of chronic, long-

term overexploitation, in 1992 the queen conch was added to Appendix II of the Convention on

International Trade in Endangered Species of Wild Fauna and Flora (CITES, 2003). CITES is

an international agreement which regulates international trade using permits to ensure all trade

is legal and will not have negative consequences for the species in the wild (CITES, 2014).

Appendix II includes species that are not yet threatened with extinction, but which may become

threatened if trade is not appropriately managed and monitored (US Fish and Wildlife Service,

2012).

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5.00%

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45.00% C

ove

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North Fore

North Back

South Back

As previously discussed, the CCMR includes designated zones, each with different imposed

governmental rules and regulations, the purpose being to protect and conserve marine

ecosystems and the wildlife found there, including the commercially important queen conch.

Conservation and Preservation zones (no-take zones) should allow commercial species, such as

the queen conch, and other species linked to their ecology, to recover, as these zones protect the

populations within them and can also contribute to stocks in the surrounding areas, such as the

General Use Zone, that permits local fishing, through either spill-over of larger individuals or

export of larvae from egg production within the reserve, thereby enhancing recruitment and

increasing the productivity of sustainable fisheries in the future (Chan et al, 2013). Ultimately,

stochastic processes such as larval transport, recruitment and the anthropogenic impacts of

fisheries make the development and management of protected areas especially complex (Stoner

et al, 2012).

In Belize there is a strict management agenda regarding the harvesting of queen conch. This

includes a regulated conch fishing season, open for nine months of the year from the 1st of

October to the 30th of June (the non-reproductive season), ensuring that harvesting does not take

place during the reproductive season. There are also restrictions on fishing with SCUBA gear

and conch size, whereby individuals with a shell length of less than 7 inches (17.8cm) or a

market clean weight of less than 3 ounces and fillet weight of less than 2.75 ounces are

prohibited from being fished (Chan et al, 2013).

Size is a useful parameter used to control and manage the overfishing of conch populations as

the shell of the queen conch provides an important function for estimating sexual maturity

(Avila-Poveda and Baqueiro-Cardenas, 2006). The thickness of the shell lips also increases with

age and thus lip thickness is commonly used in assessing age and growth rate (Horsford, 2011).

Conservation and management regime of the queen conch requires biological and ecological

knowledge of the species, including population density, structure, maturity status distribution

and shell morphology (Peel and Aranda, 2012). Due to the usefulness of shell length and lip

thickness these parameters are measured and recorded during the conch surveys conducted at

BZM.

In addition to size, it has been suggested that certain ecological characteristics of the queen

conchs amplify their vulnerability to over-fishing. In particular, juvenile conchs have been

documented aggregating in dense vegetation to reduce predation risk and thereby increase

survival probabilities (Peel and Aranda, 2012). This useful tactic has become known to local

fishermen, reducing the sustainability of their practices and leading to exploitation (Aiken et al,

2006). The basic principle associated with sustainable fishing is to capture only population

surpluses, thereby avoiding damage to the overall reproductive capacity. When overexploitation

disrupts this balance, the ecology of the population is altered, modifying mean conch size and

sex proportions and altering the age of sexual maturity (Navarrete and Valencia-Hernandez,

2013). This highlights the necessity for protected areas, managed access fishing regulations,

restrictions on size, weight and other parameters and a regular, long-term monitoring regime, for

the maintenance of healthy and sustainable queen conch populations.

This project aims to identify differences in conch density, size, and maturity status between

three sites with different levels of protection within the CCMR, specifically the General Use

Zone and the Conservation Zone. Long-term monitoring of these variables will provide insights

on the sustainability of local conch fishing practices and on the effectiveness of the multi-zone

management and closed fishing season which is currently in place in the CCMR.

4.2 Methodology

The protocol for this method has been adapted from the current method used by Belize Fisheries

Department. Since one of the aims of the project was to identify the sustainability of local queen

conch fishing practices, which involve the fishermen snorkeling and then free-diving to collect

conchs, surveys were carried out as snorkel surveys to simulate these practices. There were

three sites utilised for conch surveys, each to be surveyed every six weeks. Below is a

description of each of these conch survey sites.

Conch Site 1: (16Q 00392750 UTM 1960314) A shallow (approximately 2m deep maximum)

seagrass bed within the Conservation Zone of CCMR at the southern end of the reef. This site is

not very close to the reef, is seldom visited by tourists and is only exposed to a moderate to low

level of boat traffic.

Conch Site 2: (16Q 00392912 UTM 1960400) A shallow (approximately 2m deep maximum)

seagrass bed in the Conservation Zone within CCMR at the southern end of the reef system.

This site is also known locally as Shark and Ray Alley. As the name suggests this area has a

very large population of southern stingrays and nurse sharks and therefore is a very popular

destination for snorkel tours. This site is also relatively close to the barrier reef and a few small

patch reefs.

Conch Site 3: (16Q UTM) A shallow (approximately 2m deep maximum) seagrass bed within

the General use Zone of CCMR. This site is not very close to the reef, is seldom visited by

tourists and is exposed to a moderate level of boat traffic.

For each survey one individual was responsible for laying down the 30m transect line. Once the

transect was laid, the surveyor(s) surveyed a 2m wide belt transect (1m either side of the line)

searching for queen conchs. Each conch found inside the belt transect was collected and carried

to the boat, to avoid recording and measuring the same individual twice. Once every conch had

been collected the transect line was reeled back in and the survey team measured the total length

of each conch shell and the thickness of the lip if present, using callipers. At each site, a total of

six transects were completed, spaced approximately 10m apart. Once all the conchs had been

measured, they were placed carefully back on the sea floor at the same site where they were

found.

Once the data had been collected, conchs were divided into three maturity status categories

according to the measured lip thickness. Queen conchs with lip thickness >5mm were classified

as adults, those with a <5mm lip were classified as sub-adults, and those where the lip was

absent were classified as juveniles (Horsford, 2011).

Data regarding queen conch densities and shell length at the different study sites was analysed

using one-w A OVA w b T P H w

value of p = 0.05.


Average conch population density was highest in Site1 (26.8/100m2), followed by the popular

tourist site within the Site 2 (21.3/100m2) and lowest in Site 3(10.7/100m

2).

Table 3. Average queen conch population density at the three established sites within CCMR.

Site Average Conch Population Density/100m2

No. of Surveys Completed

Site 1 26.80556 2

Site 2 21.2963 3

Site 3 10.69444 2

Analysis of the results from each individual transect using one-way ANOVA indicated that

there is a significant difference between the three sites (F2,39 = 5 26 p = 0 0 ) T P H

test indicated that Site 3 is significantly different to Site 2 (T= 2.66, p=0.03) and Site 1 (T=-

3.01, p=0.012). In contrast, there was no significant difference between Site 2 and Site 1 (T=-

0.63, p=0.802).

Figure 7. The average Queen Conch population density/100m2 with SE bars

Average conch population density was understandably significantly higher at the two sites

within the conservation zone (Site 1 and 2), where extraction is not permitted, comparative to

the General Use Zone (Site 3), where the fishing of queen conch is legalized during open

season. This result indicates that the Conservation Zone is effective at maintaining higher

densities of queen conchs compared to the General Use Zone, where fishermen are allowed to

take conchs. It is important to maintain this level of management as the populations in the

conservation and preservation zones will help to repopulate Site 3 and rest of the General Use

Zone. Once a full year of data has been collected it will be possible to identify variations in

queen conch population density throughout the year and, in particular, to explore the differences

between conch densities before and during the closed season (July 1st to September 30

th). This

would be particularly interesting for the General Use Zone, where data on the changes in density

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during the closed season could reveal the rate at which queen conchs can repopulate the area

and reproduce.

The maturity status composition of queen conch in the surveyed sites so far showed Site1 as

having the largest proportion of Juveniles (89.6%), with the lowest percentage found in Site 3

(General Use Zone) (23.4%). A low percentage of Sub-Adults were found at all three sites (Site

1 - 2.1%, Site 2 - 7.4% and Site 3 - 0%). The largest proportions of adults were found in Site 3

(76.6%) and smallest proportion in Site 1 (8.3%).

Figure 8. Distribution of the maturity status of queen conch populations within established survey sites at

differently managed zones inside CCMR.

The limited data obtained so far suggests that very few sub-adult conchs are present, however,

Stoner et al (2012) also found low sub-adult conch populations in ecologically similar sites.

Within the two sites in the Conservation Zone (Site 1 and 2), there is a much larger proportion

of juvenile conchs compared to the General Use zone, which holds a predominantly adult conch

population (Site 3- 23.4%, Site 2- 71.5% & Site 3- 89.6%). Stoner and Ray (1993) suggested

that the juveniles aggregate together during migrations which could explain the large proportion

of juveniles in the conservation zone (sites 1 &2), which are within 100m of each other. It will

be interesting to monitor this throughout the year to understand if it is due to one juvenile

aggregation passing through or whether this is the case all year round.

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Figure 9. The average length of adult Queen Conch within established survey sites at differently

managed zones inside CCMR.

Using one-way ANOVA to compare the average adult length within the different management

zones has shown there is no significant difference between the adult lengths at different sites

(F2,80=2.66, p=0.076). However an interesting trend, for adults in Site 1 to be smaller than those

in both Site 3 (T=2.14, p=0.09) and Site 2 (T=2.14, p=0.1), has been highlighted. This trend

could reflect the fisheries department practice of releasing illegally caught, undersized conch

in the Conservation Zone rather than where they were originally harvested. Once more data

becomes available in the next phase, it will be possible to interpret these results more

confidently.

5.0 Caribbean Spiny Lobster Surveys

5.1 Introduction

The Caribbean Spiny Lobster (Panulirus argus) is the most commercially important species in

the Caribbean due to its economic value, both as a source of income and employment for the

local population, as well as foreign exchange for national government (Acosta and Robertson,

2003). Furthermore, due to the high unit prices, the international trade of lobster provides

improvements to the livelihoods of fisheries-dependent populations (Monnereau and Pollnac,

2012). In addition to their economic benefits, Caribbean spiny lobsters are also keystone

species, serving as prey for a wide range of marine animals, including; sharks, rays, turtles and

moray eels (Seudeal, 2013). In turn, they are also important predators themselves, their primary

diet consisting of molluscs (especially gastropods, chitons and bivalves) and arthropods (Cox et

al, 1997). Caribbean spiny lobsters are found in a wide range of habitats including sand,

seagrass, coral reefs and coral rubble, but has been assessed as ‘Data Deficient in the IUCN

Red List of Threatened Species, as there are gaps in the data relating to its abundance (Butler et

al, 2013). Unsustainable fishing of this species could lead to population declines and ultimately

collapse of the industry, particularly in Belize, where a decline in catch per unit effort has

150

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already been documented in the past (~1.2 kg/trap in 1965 to 0.6 kg/trap in 1997) (Butler et al,

2013).

The gregarious nature of the spiny lobsters coupled with access to abundant prey allows for

particularly high population densities, when not threatened by human overexploitation

(Behringer and Butler, 2006), suggesting that local, healthy and sustainable lobster populations

can be maintained when effective management is in place. Protected areas, similar to the

Conservation Zones found within CCMR, can function as an effective harvest refuge that ha the

potential to increase local population size, mean individual size, and consequently, reproductive

success (Acosta and Robertson, 2003).These protections should result in increased regional

larval supply and net movements of adult individuals from the reserve to adjacent fishing

grounds. In addition to the protection granted by marine reserves, lobster fishing in Belize is

currently regulated by a managed access fishing season (June 15th to February 14

th of the

following year, which is the peak of the reproductive cycle) when fishing of lobsters is not

permitted. In addition, a size limit of carapace length of 3 inches (7.6 cm) and tail weight of 4

ounces (113 g) is applied throughout the year. There is also a ban on the use of SCUBA for

catching lobsters, other gear restrictions and license limitation. Despite this, there is no current

total allowable catch quota for lobsters (Babcock, 2012).

Given the importance of the Caribbean spiny lobster at both an economic and ecosystem level,

it is essential to assess the effectiveness of the conservation efforts mentioned above, in order to

gain an insight into the sustainability of the lobster fishery. The aim of the lobster surveys

conducted by Frontier is to carry out long-term monitoring and assessment of the local

population size and structure, with regards to sex ratios and maturity status within two

differently regulated zones of CCMR; the General Use Zone, where fishing is allowed, and the

Conservation Zone, where fishing is prohibited. By comparing differences in lobster

distribution, abundance, sex and maturity status between these two areas, conclusions can be

made on the effectiveness of current conservation measures and alternative management options

can be suggested according to the findings.

In addition to vital information on the sustainability of the lobster fishery, data on lobster

distribution could potentially provide insight into the level of complexity and structure of the

local coral reef systems. This is because higher densities of Caribbean spiny lobster have shown

to be associated with areas of higher habitat complexity, where the reef is intricate and creates

crevices and hidden sites for lobsters (Rios-Lara et al, 2007). Higher lobster densities could

therefore be a used as an indicator of complex and healthy coral reefs, a feature that can also be

compared between the two different survey sites.

5.2 Methodology

For comparison purposes, in line with the aim of this study, surveys were carried out at two

different sites, one in the General Use Zone and one in the Conservation Zone. GPS location of

the survey sites were recorded in order to ensure the same sites were surveyed each time.

Surveys were carried out using an active search approach, consisting of a team of snorkelers

actively searching for lobsters without the use of fixed transects. The rationale behind this

method was to simulate local fishing practices and get an estimate of Catch Per Unit Effort

(CPUE). In other words, surveyors would find the same number of lobsters that a fisherman

would find and catch in the same area, giving an indirect indication of lobster abundance.

The survey team initially distributed sections of the survey area amongst themselves. This

minimised the overlapping of terrain and double-counting of individual lobsters whilst

surveying. All information was recorded on dive slates. Each individual snorkeled for 30

minutes looking for lobsters. Each individual lobster found was measured using a ruler to

approximate its total carapace length. Sex was also recorded, which was carried out by

determining if two extra claws were present on the back legs, or if there was an extra pair of

swimming legs underneath the tail in females. Despite best efforts it was often not possible to

m b x b ock crevices,

with their abdomen not visible to the surveyor. Lobster were not handled in order to minimize

disturbance. If lobsters escaped before measurements could be made, these were estimated by

sight.

As there were differences in the number of snorkelers participating in each survey, each

individual active search carried out at the same site was counted as a separate survey in order to

avoid bias.


Table 4. Data collected from lobster surveys conducted from the two established and differently regulated

sites within Caye Caulker Marine Reserve.

General Use Zone Conservation Zone

Date Number of

individuals

sighted

Carapace

length

(cm)

Sex Date Number of

individuals

sighted

Carapace

length

(cm)

Sex

13/09/2014 2 10 Unknown 13/09/2014 2 12 M

7 F 9 F

28/09/2014 0 NA NA

31/09/2014 1 17 Unknown 05/09/2014 0 NA NA

31/09/2014 0 NA NA

31/09/2014 0 NA NA

Seven lobster surveys have been completed up to date (five in the General Use Zone and two in

the Conservation Zone), therefore the data is still too limited to make any inferences about the

current status, maturity and sexual distribution of the populations within CCMR. A maximum

number of two lobsters were found during the surveys, so it is yet to be determined if this results

from the ability to locate these elusive species, or if these results are a normal representation of

lobster populations at the sites. Bi-monthly lobster surveys will continue during the next phase

and should produce enough data to formulate statistically supported observations and trends in

lobster populations.

6.0 Seagrass Monitoring

6.1Introduction

As BZM is still within its first six months, more time is needed to solidify methodology and

perform preliminary surveys for other projects, such as, the Seagrass monitoring project, which

will be properly initiated during the next phase.

Seagrasses act as ecosystem engineers, profoundly influencing the physical, chemical and

biological environments within coastal waters. Seagrasses alter water flow, nutrient cycling and

food web dynamics and stabilise sediments (Orth, et al., 2006). They are also a vital food source

for mega-herbivores in the Caribbean, including the green, loggerhead and hawksbill sea turtles

(Chelonia mydas, Caretta caretta and Eretmochelys imbricata respectively) and West Indian

Manatees (Trichechus manatus), all being of international conservation concern (Beck et al,

2001). They provide a critical habitat; nursery and refuge area for juvenile fish and other

commercially and recreationally important fishery species and allow trophic transfers to

adjacent habitats in tropical and temperate regions (Heck et al, 2003).

Seagrasses are currently threatened from rapid environmental changes, as a consequence of

increasing coastal human population pressures and climate change (Lotze, 2006). The most

widely accepted disturbances include sediment and nutrient runoff, physical damage, invasive

species, disease, commercial fishing practices, aquaculture, overgrazing, algal blooms, and

global warming associated impacts (Orth, et al., 2006). Such disturbances have resulted in the

recent decline of seagrass meadows in the region and ultimately increase the necessity for the

protection, monitoring and management of this relatively understudied ecosystem.

6.2 Aims and Objectives

The implementation of monthly seagrass surveys in this area will allow monitoring of the health

of the Seagrass throughout the development of Caye Colony, a new site for residential

development alongside the forest reserve on the northern island of Caye Caulker. By surveying

one site alongside the developing area and another adjacent to the forest reserve, data can be

compared between the two sites, as well as monitored over time. It is expected to see a change

in the density of Seagrass at the site alongside Caye Colony development.

6.3 Methodology

The method that will be used has been adapted from the Seagrass Monitoring Network protocol,

which has also been used by The Belize Fisheries Department. Unlike the Seagrass Monitoring

Network protocol, transects will be 30m and not be permanently marked so that data collection

is feasible with the resources and time available to Frontier.

Six transects of 30m will be carried out at each site; near shore (A), centre (B) and offshore (C)

within water approximately <1m, 1.5-3m and 3-5m deep respectively. For each site there will be

a 'peg', the start point for each quadrat will lie at 5 m intervals to the south of the peg. The

transect will then be laid perpendicular to the shore and away from the shore. The 50cm x 50cm

quadrat will be placed at 10 m intervals to the right of the transect line. For each quadrat, the

total percentage cover of each sea grass species present is recorded, followed by the maximum

canopy height of each species and the presence of grazing will be noted. Within each quadrat

another 25cm x 25cm quadrat is placed within the bottom left corner closest to the beginning of

the meter mark. Within this quadrat the presence and number of any flowers observed on each

species will be recorded, as well as the total number of rhizome nodes for each species. If the

rhizome node is beneath the surface individual blades will be counted. Each site should be

surveyed every 6 weeks (Short et al, 2006).

In addition to this, one trained individual will be responsible for counting and recording the fish

and invertebrate species present within a 1m band of the transect. The size of each fish recorded

is estimated by assigning them to the following size categories (<5cm, 5-15, 16-30, 31-40, >40)

and number observed will be recorded. Such data collection could be used to supplement the

information on the health of the seagrass beds in the area and will allow for comparisons to be

made between the undeveloped and the developing site.

7.0 Mangrove Monitoring

6.1 Introduction

There are three mangrove species found in Belize; Red mangrove (Rhizophora mangle), Black

mangrove (Avicennia germinans) and the White mangrove (Laguncularia racemosa).

Buttonwood (Conocarpus erectus) is also a species associated with the mangrove community,

although its lack of aerial roots means it is not classed as a mangrove. The mangrove ecosystem

has great ecological and socio-ecological value. The structural complexity of the above ground

roots provide shelter from predation for many juvenile fish species, which depend on shallow

water biotopes as a nursery (Nagelkerken et al, 2000). Mangroves act as a filtering system,

removing harmful heavy metals, nutrients and sediment before they can reach the open ocean,

where they can cover and harm the coral reefs. This can buffer some of the damage from

anthropogenic activities, such as, mining and the use of fertilizers (Ellison & Farnsworth, 1996).

Furthermore, they protect the land from soil erosion and act as a defense against the damage

caused by storms and hurricanes (Badola & Hussain, 2005). Despite socio-ecological values,

this habitat is facing many anthropogenic disturbances, such as, extraction, pollution,

reclamation and climate change (Ellison & Farnsworth, 1996).

Caye Caulker forest reserve is surrounded by mangroves, however, this site has suffered from

the impact of Hurricane Keith (Cat.4- 2000), removal for agricultural purposes (coconut

production) and more recently, removal for housing and resort building at the new development

site, Caye Colony. Despite these negative effects, there were two large sites of mangrove

restoration implemented by FAMRACC after Hurricane Kieth (McRae, 2010). Therefore, the

mangroves in this area are in various stages of recovery and decline.


The monitoring of mangroves in the Caye Caulker Forest Reserve aims to understand the

impact of development alongside the forest reserve, as well as the impacts of restoration efforts.

To do this the above ground biomass at the restoration area and area adjacent to the

development site will be monitored over time. If the restoration sites are successful an increase

in above ground biomass will be recorded. Furthermore, if there is successful management of

the new development site, Caye Colony, no change in the adjacent mangroves above ground

biomass will be recorded.

6.3 Methodology

Transect lines, from the seaward margin of the mangrove forest perpendicular to the shore and

up to the terrestrial edge of the mangrove forest will be conducted. The transect will then be

divided into zones corresponding to the level of tidal inundation i.e. Low (always below water),

Mid (intertidal) & High (only submerged at spring tides). Within each zone two to three 5m x

5m rope quadrats are taken. Within each quadrat the surveyor will record salinity, leaf litter

depth, number of adults (girth greater than 4cm and greater than 1m tall) of each species

present, number of saplings (girth less than 4cm and greater than 1m tall) of each species

present and number of seedlings (height less than 1m) of each species present. For the adults of

each species present, the girth at breast height will be measured according to the procedure by

English et al (1994);

When a tree forks below breast height, or sprouts from a single base close to the ground

or above it, measure each branch as a separate stem.

When the stem forks at breast height or slightly above it measure the girth at breast

height or just below the swelling caused by the fork.

When the stem has prop roots or a fluted lower trunk, measure the girth 20cm above the

root collar.

When the stem has swelling, branches or abnormalities at the point of measurement,

take the diameter slightly above or below the irregularity, where it stops affecting

normal form.

The girth measurement can then be converted into the diameter measurement at breast

( H) b b π (3.14). English et al, (1994) outlines an allometric

relationship between DBH and the individual plants above ground biomass, which can then

be used to calculate the above ground biomass for each species (Frontier Madagascar,

2005).

8.0 Marine Debris Monitoring

8.1Introduction

M b “ m terials of human origin; that are discarded at sea, reach the

w w m ( A m S

1975). The source of marine debris is normally classified as either land or ocean and waterway

based (Sheavly & Register, 2007). Land-based sources of marine debris include dumpsites in

coastal areas or river banks, industrial outfalls, material manufacturers, processors or

transporters, sewage treatment and drain overflows, tourism and recreational use of coastal

areas. These land-based sources of debris account for 80% of the global marine pollution

(Sheavly & Register, 2007). Ocean and waterway-based sources include shipping (merchant,

public transport, naval and research vessels) and fishing vessels, angling, fish farming,

discarded and lost fishing gear, oil and gas platforms, undersea exploration, legal and illegal

dumping at sea and natural disasters. The growing use of synthetic polymers means that debris

is building up faster than it can degrade; many of which are buoyant and can negatively impact

even the remotest areas (Moore, 2008). Coral reefs suffer from abrasion and smothering from

marine debris, many faunal species accidentally ingest debris, discarded and lost fishing gear

can entangle wildlife, and medicinal waste can carry diseases (Gregory, 2009).


Identifying the source of marine debris locally and globally through project AWARE beach

clean surveys, will help to make appropriate decisions on how to mitigate and manage this

threat. The results from these surveys can then be used to contact local businesses that may be a

source of the marine debris e.g. fishing tours, if there is a significant amount of angling debris is

recorded.

8.3 Methodology

Marine debris monitoring in the form of Beach cleanups will be conducted using an existing

Data Card produced by Project AWARE (Barnett, 2015). Preliminary information recorded in

the Data Card are divided into three main sections presented in Table 5.

Table 5. Sections of the Data Card used during beach cleanups (Barnett, 2015).

Section Contents

1. Cleanup site information Location, Date, Number of people involved,

Distance cleaned, Number of trash bags filled,

Estimated weight collected, Estimated time

spent on cleanup

2. Contact information Names and email addresses of team members

3. Entangled animals List of all entangled animals found during the

cleanup, if they were alive or dead and the

nature of the entanglement debris

The following section in the Data Card contains information on the source of marine debris and

it is divided in five categories: Shoreline and recreational activities, Ocean and waterway

activities, Smoking-related activities, Dumping activities and Medical and personal hygiene.

Survey participants walk along the coastline and collect all debris they find. Every item

collected is assigned to one of the above categories and a count of the items belonging to each

of the categories is kept using tally marks.

9.0 Community Work and Public Awareness

Contributions to community work have recently begun, with the BZM team taking part in

weekly beach and trail clean ups both around the base camp and on the Woodrail Trail (the

public trail within the forest reserve) co-managed by FAMRACC.

The local high school is starting a variety of lesson to help the students to decide on a career

path, one of the career paths they have chosen is Marine Biology and they have asked the

fisheries biologist to conduct weekly lessons, both practical and in-class. A Frontier staff

member will assist with the pitch to the school year on the 9th January 2015. Once the students

have decided on which career lesson they will be participating in the classes will commence late

January on either Tuesdays or Thursdays. BZM volunteers will able to assist these classes and

help the children with fish, coral and invertebrate ID.

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11.0 Appendices

11.1 Appendix 1.

Species Lists

Fish Species List

Angelfish- Pomacanthidae

Queen Angelfish Holacanthus ciliaris

Blue Angelfish Holacanthus bermudensis

French Angelfish Pomacanthus paru

Gray Angelfish Pomacanthus arcuatus

Rock Beauty Holacanthus tricolor

Butterflyfish- Chaetodontidea

Banded Butterflyfish Chaetodon striatus

Foureye Butterflyfish Chaetodon capistratus

Spotfin Butterflyfish Chaetodon ocellatus

Reef Butterflyfish Chaetodon sedentarius

Longsnout Butterflyfish Prognathodes aculeatus

Surgeonfish- Acanthuridae

Blue Tang Acanthurus coeruleus

Ocean Surgeonfish Acanthurus tractus

Doctorfish Acanthurus chirurgus

Jacks- Carangidae

Bar Jack Caranx ruber

Permit Trachinotus falcatus

Grunts- Haemulidae

French Grunt Haemulon flavolineatum

Bluestriped grunt Haemulon sciurus

Smallmouth Grunt Haemulon chrysargyreum

White Grunt Haemulon plumierii

Caesar Grunt Haemulon carbonarium

Spanish Grunt Haemulon macrostomatum

Tomtate Haemulon aurolineatum

Cottonwick Haemulon melanurum

Striped Grunt Haemulon striatum

Sailors Choice Haemulon parra

Porkfish Anisotremus virginicus

Black Margate Anisotremus surinamensis

White Margate Haemulon album

Snappers- Lutjanidae

Red Snapper Lutjanus campechanus

Mutton Snapper Lutjanus analis

Cubera Snapper Lutjanus cyanopterus

Gray Snapper Lutjanus griseus

Dog Snapper Lutjanus jocu

Mahogany Snapper Lutjanus mahogoni

Lane Snapper Lutjanus synagris

Yellowtail Snapper Ocyurus chrysurus

Schoolmaster Lutjanus apodus

Groupers-Serranidae

Goliath Grouper Epinephelus itajara

Nassau Grouper Epinephelus striatus

Red Grouper Epinephelus morio

Graysby Cephalopholis cruentata,

Red Hind Epinephelus guttatus

Rock Hind Epinephelus adscensionis

Coney Epinephelus fulvus

Black Grouper Mycteroperca bonaci

Tiger Grouper Mycteroperca tigris

http://en.wikipedia.org/wiki/Epinephelus

Yellowmouth Grouper Mycteroperca interstitialis

Yellowfin Grouper Mycteroperca venenosa

Parrotfish- Scaridae

Blue Parrotfish Scarus coeruleus

Midnight Parrotfish Scarus coelestinus

Rainbow Parrotfish Scarus guacamaia

Queen Parrotfish Scarus vetula

Stoplight Parrotfish Sparisoma viride

Princess Parrotfish Scarus taeniopterus

Striped Parrotfish Scarus iseri

Redband Parrotfish Sparisoma aurofrenatum

Redtail Parrotfish Sparisome chrysopterum

Yellowtail Parrotfish Sparisoma rubripinne

Greenblotch Parrotfish Sparisoma atomarium

Trunkfish- Ostraciidae

Spotted Trunkfish Lactophrys bicaudalis

Triggerfish & Filefish- Balistidae

Queen Triggerfish Balistes vetula

Ocean Triggerfish Canthidermis sufflamen

Black Durgon Melicthys niger

Scrawled Filefish Aluterus scriptus

Whitespotted Filefish Cantherhines macrocerus

Orangespotted Filefish Cantherhines pullus

Miscellaneous

Hogfish Lachnolaimus maximus

Spanish Hogfish Bodianus rufus

Chub Kyphosus sectatrix/incisor

Great Barracuda Sphyraena barracuda

Yellowtail Damselfish Microspathodon chrysurus

Lionfish Pterois volitans

Juveniles and Recruits Fish Species List

Damselfish (<3.5cm)

Longfin Damselfish Stegastes diencaues

Dusky Damselfish Stegastes adustus

Threespot Damselfish Stegastes planifrons

Cocoa Damselfish Stegastes variabilis

Bicolor Damselfish Stegastes partitus

Blue Chromis Chromis cyanea

Brown Chromis Chromis multilineata

Surgeonfish (<5cm)

Blue Tang Acanthurus coeruleus

Ocean Surgeonfish Acanthurus tractus

Butterflyfish (<2.5cm)

Banded Butterflyfish Chaetodon striatus

Foureye Butterflyfish Chaetodon capistratus

Parrotfish

Princess Parrotfish Scarus taeniopterus

Striped Parrotfish Scarus iseri

Redband Parrotfish Sparisoma aurofrenatum

Greenblotch Parrotfish Sparisoma atomarium

Stoplight Parrotfish Sparisoma viride

Others (<3.5cm)

Spanish Hogfish Bodianus rufus

Slippery Dick Halichoeres bivittatus

Clown Wrasse Halichoeres maculipinna

Rainbow Wrasse Halichoeres pictus

Yellowhead Wrasses Halichoeres garnoti

Bluehead Wrasse Thalassoma bifasciatum

Fairy Basslet Gramma loreto

Benthic Species List and Their Corresponding Codes

Corals

Branching Fire Coral- MALC

Blade Fire Coral- MCOM

Gorgonian- GG

Staghorn Coral- ACER

Fused Staghorn Coral- APRO

Elkhorn Coral- APAL

Clubtip Finger Coral- PPOR

Pillar Coral- DCYL

Blushing Star Coral- SINT

Lobed Star Coral- OANN

Mountainous Star Coral- OFAV

Great Star Coral- MCAV

Elliptical Star Coral- DSTO

Mustard Hill Coral- PAST

Massive Starlet Coral- SSID

Lesser Starlet Coral- SRAD

Symmetrical Brain Coral- PSTR

Knobby Brain Coral- PCLI

Grooved Brain Coral- DLAB

Maze Coral- MMEA

Rose Coral- MARE

Boulder Brain Coral- CNAT

Whitestar Sheet Coral- ALAM

Lettuce Coral- AAGA

Low Relief Lettuce Coral- AHUM

Thin Relief Lettuce Coral- ATEN

Ridged Cactus Coral- MLAM

Sinuous Cactus Coral- ISIN

Spiny Flower Coral- MANG

Smooth Flower Coral- EFAS

Sponges- SPN

Marine Plants and Algae

Thalassia sp.- TH

Dictyota sp. - DT

Lobophora sp.- LOB

Halimeda sp. HA

Blue/Green Algae- BGA

Turf Algae- TURF

Macro Algae- MAC

Coralline Algae- ACOR

Other Substrates

Sand- SN

Bare Rock- BR

11.2 Appendix

Table 6. Average percentage cover of benthic species and substrate

North Fore North Back South Fore South Back

HC 11.67% 16.07% 0.00% 40.83%

SS 25.42% 13.57% 0.00% 0.00%

GG 18.33% 13.57% 0.00% 8.33%

SPN 1.67% 4.05% 0.00% 7.50%

FA 28.33% 23.81% 0.00% 20.00%

Acropora sp.

0.00% 0.00% 0.00% 0.83%

Millepora sp

1.46% 4.29% 0.00% 7.50%

11.3 Appendix

Table 7. Average percentage dead coral of all the species characterised from the four defined

sites.

North Back North Fore South Back South Fore

AAGA 40.00 15.00

ACER 70.00

AHUM 1.25 0.00 20.00

ATEN 15.00 5.00

CNAT 0.00

DCYL 0.00 0.00 0.00

DLAB 0.00

DSTO 0.00 0.00

EFAS 3.00

GG 0.00 0.00

IRIG 0.00

MALC 1.67 0.00 0.00

MARE 40.00

MCAV 0.00 0.00

MCOM 0.00

MLAM 3.89 0.00

MMEA 0.00 0.00

OANN 5.00 0.00

OFAV 9.00 5.00 15.00

PAST 4.57 22.50

PCLI 5.00 0.00

PPOR 17.50 25.00 60.00 0.00

PSTR 0.00 0.00 40.00

SINT 15.00 0.00

SRAD 0.71 2.50

SSID 7.50 0.00

Appendix

Table. Average number of fish wit in the size range or category in the four survey sites.


6-10 cm 22.67 8.00 0.00 45.00

11-20 cm 18.00 5.00 0.00 21.00

21-30 cm 1.33 1.00 0.00 8.00

31-40 cm 0.33 0.00 0.00 2.00

>40cm 0.33 0.00 0.00 0.00

Herbivores 13.33 15.43 0.00 61.00

Commercial 1.67 0.57 0.00 2.00

11.4 Appendix

Table 8. Average number of each juvenile fish species present in the four survey sites.


Longfin Damselfish 1.00 0.00 0.00 0.00

Dusky Damselfish 2.00 1.50 0.00 0.00

Threespot Damselfish 1.00 0.50 0.00 0.00

Cocoa Damselfish 0.00 0.33 0.00 0.00

Bicolor Damselfish 4.50 3.17 0.00 19.00

Yellowtail Damselfish 2.00 2.00 0.00 0.00

Blue Chromis 4.00 0.00 0.00 2.00

Brown Chromis 0.00 0.00 0.00 0.00

Blue Tang 1.00 0.17 0.00 0.00

Ocean Surgeonfish 0.00 0.00 0.00 1.00

Banded Butterflyfish 0.00 0.00 0.00 0.00

Four-eye Butterflyfish 0.00 0.33 0.00 0.00

Striped Parrotfish 13.00 8.67 0.00 17.00

Princess Parrotfish 4.00 4.17 0.00 16.00

Redband Parrotfish 0.00 0.00 0.00 3.00

Greenblotch Parrotfish 0.00 1.00 0.00 0.00

Stoplight Parrotfish 0.00 0.50 0.00 8.00

Spanish Hogfish 1.00 0.50 0.00 0.00

Slippery Dick 6.50 2.50 0.00 0.00

Clown Wrasse 0.00 0.33 0.00 2.00

Rainbow Wrasse 0.00 0.17 0.00 0.00

Yellowhead Wrasses 1.00 0.33 0.00 4.00

Bluehead Wrasse 12.67 4.67 0.00 9.00

Fairy Basslet 0.00 0.00 0.00 0.00

11.5 Appendix

Table 9. Density/100m2 form each Queen Conch survey

Date Site Total Density/100m2

24.10.14 GUZ 37 10.27777778

31.10.14 SRA 97 26.94444444

16.08.14 SRA 75 20.83333333

26.07.14 CZ 76 21.11111111

30.08.14 GUZ 40 11.11111111

20.09.14 CZ 117 32.5

27.09.14 SRA 58 16.11111111

11.6 Appendix

Table 10. Maturity status of Queen Conch populations at the three define survey sites within

the CCMR

GUZ SRA CZ

Juveniles 23.38% 71.48% 89.64%

Sub-Adults 0.00% 7.42% 2.07%

Adults 76.62% 21.09% 8.29%

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