Click
here to close Hello! We notice that
you are using Internet Explorer, which is not supported by Echinobase
and may cause the site to display incorrectly. We suggest using a
current version of Chrome,
FireFox,
or Safari.
PLoS One
2017 Jan 01;1212:e0188515. doi: 10.1371/journal.pone.0188515.
Show Gene links
Show Anatomy links
Partitioning no-take marine reserve (NTMR) and benthic habitat effects on density of small and large-bodied tropical wrasses.
Russ GR
,
Lowe JR
,
Rizzari JR
,
Bergseth BJ
,
Alcala AC
.
???displayArticle.abstract???
No-take marine reserves (NTMRs) are increasingly implemented for fisheries management and biodiversity conservation. Yet, assessing NTMR effectiveness depends on partitioning the effects of NTMR protection and benthic habitat on protected species. Such partitioning is often difficult, since most studies lack well-designed sampling programs (i.e. Before-After-Control-Impact-Pair designs) spanning long-term time scales. Spanning 31 years, this study quantifies the effects of NTMR protection and changes to benthic habitat on the density of tropical wrasses (F. Labridae) at Sumilon and Apo Islands, Philippines. Five species of wrasse were studied: two species of large-bodied (40-50 cm TL) Hemigymnus that were vulnerable to fishing, and three species of small-bodied (10-25 cm TL) Thalassoma and Cirrhilabrus that were not targeted by fishing. NTMR protection had no measurable effect on wrasse density, irrespective of species or body size, over 20 (Sumilon) and 31 (Apo) years of protection. However, the density of wrasses was often affected strongly by benthic cover. Hemigymnus spp. had a positive association with hard coral cover, while Thalassoma spp. and Cirrhilabrus spp. had strong positive associations with cover of rubble and dead substratum. These associations were most apparent after environmental disturbances (typhoons, coral bleaching, crown of thorns starfish (COTS) outbreaks, use of explosives and drive nets) reduced live hard coral cover and increased cover of rubble, dead substratum and sand. Disturbances that reduced hard coral cover often reduced the density of Hemigymnus spp. and increased the density of Thalassoma spp. and Cirrhilabrus spp. rapidly (1-2 years). As hard coral recovered, density of Hemigymnus spp. often increased while density of Thalassoma spp. and Cirrhilabrus spp. often decreased, often on scales of 5-10 years. This study demonstrates that wrasse population density was influenced more by changes to benthic cover than by protection from fishing.
???displayArticle.pubmedLink???
29216194
???displayArticle.pmcLink???PMC5720769 ???displayArticle.link???PLoS One
Fig 1. Location of the study sites in the central Philippines.Inset A: Sumilon Island. Inset B: Apo Island. Crosshatching indicates no-take marine reserve area. Black rectangles show approximate positions of permanent 50 m * 20 m replicate transects for fish and benthic surveys.
Fig 2. Long-term (1983–2014) trends of H. melapterus density.a) Sumilon NTMR and fished sites, b) Apo NTMR and fished sites. Error bars are standard error (SE). Trend lines are polynomials.
Fig 3. Long-term temporal trends in density of (a) H. melapterus, (b) H. fasciatus, (c) T. hardwickii (1999–2014), (d) T. lunare (2000–2014), (e) Cirrhilabrus spp., and temporal trends in cover of hard corals (CBCT and CMCE combined) at Apo fished and NTMR (reserve) sites.Wrasse density is shown by black points and continuous trend lines. Hard coral cover is shown by white data points and dotted trend lines. Environmental disturbance events are indicated by arrows: 1998 coral bleaching event–white, 2011 and 2012 typhoon events–black. Standard errors (SE) are displayed on plots, along with polynomial trend lines.
Fig 4. Long-term temporal trends in density of (a) H. melapterus, (b) H. fasciatus, (c) T. hardwickii (1999–2014), (d) T. lunare (1983–1999), (e) Cirrhilabrus spp., and temporal trends in cover of hard corals (CBCT and CMCE combined) at Sumilon fished and NTMR (reserve) sites.Wrasse density is shown by black points and continuous trend lines. Hard coral cover is shown by white data points and dotted trend lines. Environmental disturbance events are indicated by arrows: 1984 to 1986 destructive fishing event–grey, 1998 coral bleaching event–white, 2012 typhoon event–black. Standard errors (SE) are displayed on plots, along with polynomial trend lines.
Fig 5. Non-metric multidimensional scaling (nMDS) performed on distance matrices of benthic cover and wrasse assemblage structure.a) Assemblage structure of the benthos at Sumilon and Apo Islands, b) assemblage structure of wrasses at Sumilon and Apo Islands. Black shapes represent fished sites, white shapes represent NTMR sites. Benthic components include: DS = dead substratum, HC = hard coral (CBCT and CMCE combined), SC = soft coral, SCI = structural complexity. Assemblage shifts from HC to DS dominance post-2011 and2012 typhoon events at Apo NTMR and Sumilon fished sites are indicated by an eclipse.
Alcala,
No-take marine reserves and reef fisheries management in the Philippines: a new people power revolution.
2006, Pubmed
Alcala,
No-take marine reserves and reef fisheries management in the Philippines: a new people power revolution.
2006,
Pubmed
Babcock,
Decadal trends in marine reserves reveal differential rates of change in direct and indirect effects.
2010,
Pubmed
De'ath,
The 27-year decline of coral cover on the Great Barrier Reef and its causes.
2012,
Pubmed
,
Echinobase
Edgar,
Global conservation outcomes depend on marine protected areas with five key features.
2014,
Pubmed
Emslie,
Retention of habitat complexity minimizes disassembly of reef fish communities following disturbance: a large-scale natural experiment.
2014,
Pubmed
Emslie,
Expectations and Outcomes of Reserve Network Performance following Re-zoning of the Great Barrier Reef Marine Park.
2015,
Pubmed
Graham,
Extinction vulnerability of coral reef fishes.
2011,
Pubmed
Graham,
Predicting climate-driven regime shifts versus rebound potential in coral reefs.
2015,
Pubmed
Graham,
Lag effects in the impacts of mass coral bleaching on coral reef fish, fisheries, and ecosystems.
2007,
Pubmed
Graham,
Dynamic fragility of oceanic coral reef ecosystems.
2006,
Pubmed
Halpern,
Spatial and temporal changes in cumulative human impacts on the world's ocean.
2015,
Pubmed
Hughes,
Coral reefs in the Anthropocene.
2017,
Pubmed
Hughes,
Global warming and recurrent mass bleaching of corals.
2017,
Pubmed
Jackson,
Historical overfishing and the recent collapse of coastal ecosystems.
2001,
Pubmed
Jones,
Coral decline threatens fish biodiversity in marine reserves.
2004,
Pubmed
Komyakova,
Relative importance of coral cover, habitat complexity and diversity in determining the structure of reef fish communities.
2013,
Pubmed
McClanahan,
Effects of the 1998 coral morality event on Kenyan coral reefs and fisheries.
2002,
Pubmed
,
Echinobase
McClanahan,
Critical thresholds and tangible targets for ecosystem-based management of coral reef fisheries.
2011,
Pubmed
McCook,
Adaptive management of the Great Barrier Reef: a globally significant demonstration of the benefits of networks of marine reserves.
2010,
Pubmed
,
Echinobase
Newton,
Current and future sustainability of island coral reef fisheries.
2007,
Pubmed
Paśko,
Tool-like behavior in the sixbar wrasse, Thalassoma hardwicke (Bennett, 1830).
2010,
Pubmed
Sandin,
Baselines and degradation of coral reefs in the Northern Line Islands.
2008,
Pubmed
Soler,
Reef Fishes at All Trophic Levels Respond Positively to Effective Marine Protected Areas.
2015,
Pubmed
Westneat,
Local phylogenetic divergence and global evolutionary convergence of skull function in reef fishes of the family Labridae.
2005,
Pubmed
