were captured. It seems that, as result of these large extractions, catches and
production decreased from 1,153 sea cucumbers boat
-1 d
-1 in 1999 to 350 sea
cucumbers boat
-1 d
-1 in 2002 (Alfonso et al. 2003).
Due to major decrease in resources in zones like Bahía de Banes, Banco
Chinchorro, and Cayos de Manzanillo, the MIP established several regulations.
These included a fishing ban in affected regions, fishing effort limits regarding to
previous evaluations by zone, minimal size of 220 mm total length, a fishing ban
during the peak months in reproduction (February–April), and a rotation system of
catch areas. As a result of these measures, a resource recovery was observed in
2005 in every fishing zone in the country, including the most affected ones
(Alfonso 2004; Alfonso et al. 2004, 2005, pers. comm. R. Castelo).
12.6 Threats
The main threats affecting echinoderms of the Cuban Archipelago are closely
related to habitat destruction, fundamentally caused by coastal development and/or
natural factors (e.g. hurricanes, cyclones, etc.).
The known effect in Cuba is related to the sea urchin D. antillarum populations.
The mass mortality of D. antillarum has been widely documented, not only in
Cuba but all along the Caribbean region (Hughes et al. 1999; Alcolado et al. 2004).
In many reefs from the Cuban Archipelago, an excessive growth of algae has been
observed (Habana littoral; Sabana-Camagüey Archipelago; Largo, Paraíso, and
Levisa Cays; and nearby Bahía Honda). This seems to be, in general terms, due to
the mass mortality of D. antillarum and also because of the obvious low numbers
of herbivore fishes.
Alcolado et al. (2004) studied population densities of D. antillarum in 199 sites
at different reef ridges from the Cuban Archipelago. They showed that, even
though D. antillarum existed in some sites in ecozones Jardines de la Reina
(0.925–21.1 ind m
-2 ) and in Golfo de Batabanó (0.58 a 1.17 ind m
-2 ) with
densities ranging from moderate to very high, the recovery of populations of this
species is happening slowly. Caballero et al. (2007) mentioned that D. antillarum
density in ‘‘María La Gorda’’ reef (Bahía de Corrientes) was very low
(3.5 ind 10 m
-2 ).
Martín-Blanco et al. (2011) presented the results of a study about abundance,
distribution, and size structure of D. antillarum in 22 frontal reefs from Jardines de
la Reina Archipelago. The authors found that D. antillarum densities were large in
reef ridges (0.08–2.18 ind m
-2 ) and decreased down to three orders of magnitude,
with a maximum density of 0.13 ind m
-2 on the slope. These authors concluded
that the size frequency distribution of D. antillarum suggests that recruiting began
to be evident approximately 3 years prior to the sampling; indicating that their
populations were affected during the past and are now recovering.
Another species that seems to have been affected in some way is the sea urchin
A. punctulata, for it was highly abundant in the northern coast of Cuba, especially
418
R. d. Valle-García et al.
production decreased from 1,153 sea cucumbers boat
-1 d
-1 in 1999 to 350 sea
cucumbers boat
-1 d
-1 in 2002 (Alfonso et al. 2003).
Due to major decrease in resources in zones like Bahía de Banes, Banco
Chinchorro, and Cayos de Manzanillo, the MIP established several regulations.
These included a fishing ban in affected regions, fishing effort limits regarding to
previous evaluations by zone, minimal size of 220 mm total length, a fishing ban
during the peak months in reproduction (February–April), and a rotation system of
catch areas. As a result of these measures, a resource recovery was observed in
2005 in every fishing zone in the country, including the most affected ones
(Alfonso 2004; Alfonso et al. 2004, 2005, pers. comm. R. Castelo).
12.6 Threats
The main threats affecting echinoderms of the Cuban Archipelago are closely
related to habitat destruction, fundamentally caused by coastal development and/or
natural factors (e.g. hurricanes, cyclones, etc.).
The known effect in Cuba is related to the sea urchin D. antillarum populations.
The mass mortality of D. antillarum has been widely documented, not only in
Cuba but all along the Caribbean region (Hughes et al. 1999; Alcolado et al. 2004).
In many reefs from the Cuban Archipelago, an excessive growth of algae has been
observed (Habana littoral; Sabana-Camagüey Archipelago; Largo, Paraíso, and
Levisa Cays; and nearby Bahía Honda). This seems to be, in general terms, due to
the mass mortality of D. antillarum and also because of the obvious low numbers
of herbivore fishes.
Alcolado et al. (2004) studied population densities of D. antillarum in 199 sites
at different reef ridges from the Cuban Archipelago. They showed that, even
though D. antillarum existed in some sites in ecozones Jardines de la Reina
(0.925–21.1 ind m
-2 ) and in Golfo de Batabanó (0.58 a 1.17 ind m
-2 ) with
densities ranging from moderate to very high, the recovery of populations of this
species is happening slowly. Caballero et al. (2007) mentioned that D. antillarum
density in ‘‘María La Gorda’’ reef (Bahía de Corrientes) was very low
(3.5 ind 10 m
-2 ).
Martín-Blanco et al. (2011) presented the results of a study about abundance,
distribution, and size structure of D. antillarum in 22 frontal reefs from Jardines de
la Reina Archipelago. The authors found that D. antillarum densities were large in
reef ridges (0.08–2.18 ind m
-2 ) and decreased down to three orders of magnitude,
with a maximum density of 0.13 ind m
-2 on the slope. These authors concluded
that the size frequency distribution of D. antillarum suggests that recruiting began
to be evident approximately 3 years prior to the sampling; indicating that their
populations were affected during the past and are now recovering.
Another species that seems to have been affected in some way is the sea urchin
A. punctulata, for it was highly abundant in the northern coast of Cuba, especially
418
R. d. Valle-García et al.