Estuarine, Coastal and Shelf Science (2000) 51, 31–44
doi:10.1006/ecss.2000.0617, available online at http://www.idealibrary.com on
Importance of Mangroves, Seagrass Beds and the
Shallow Coral Reef as a Nursery for Important Coral
Reef Fishes, Using a Visual Census Technique
I. Nagelkerkena,b, G. van der Veldea,d, M. W. Gorissena, G. J. Meijera, T. van’t Hof c
and C. den Hartoga
a
Laboratory of Aquatic Ecology, Aquatic Animal Ecology, University of Nijmegen, Toernooiveld 1,
6525 ED Nijmegen, The Netherlands
b
Carmabi Foundation, P.O. Box 2090, Piscaderabaai z/n, Curaçao, Netherlands Antilles
c
Marine and Coastal Resource Management, The Bottom, Saba, Netherlands Antilles
Received 19 August 1999 and accepted in revised form 29 February 2000
The nursery function of various biotopes for coral reef fishes was investigated on Bonaire, Netherlands Antilles. Length
and abundance of 16 commercially important reef fish species were determined by means of visual censuses during the
day in six different biotopes: mangrove prop-roots (Rhizophora mangle) and seagrass beds (Thalassia testudinum) in Lac
Bay, and four depth zones on the coral reef (0 to 3 m, 3 to 5 m, 10 to 15 m and 15 to 20 m). The mangroves, seagrass
beds and shallow coral reef (0 to 3 m) appeared to be the main nursery biotopes for the juveniles of the selected species.
Mutual comparison between biotopes showed that the seagrass beds were the most important nursery biotope for juvenile
Haemulon flavolineatum, H. sciurus, Ocyurus chrysurus, Acanthurus chirurgus and Sparisoma viride, the mangroves for
juvenile Lutjanus apodus, L. griseus, Sphyraena barracuda and Chaetodon capistratus, and the shallow coral reef for juvenile
H. chrysargyreum, L. mahogoni, A. bahianus and Abudefduf saxatilis. Juvenile Acanthurus coeruleus utilized all six biotopes,
while juvenile H. carbonarium and Anisotremus surinamensis were not observed in any of the six biotopes. Although fishes
showed a clear preference for a specific nursery biotope, most fish species utilized multiple nursery biotopes
simultaneously. The almost complete absence of juveniles on the deeper reef zones indicates the high dependence of
juveniles on the shallow water biotopes as a nursery. For most fish species an (partial) ontogenetic shift was observed at
a particular life stage from their (shallow) nursery biotopes to the (deeper) coral reef. Cluster analyses showed that closely
related species within the families Haemulidae, Lutjanidae and Acanthuridae, and the different size classes within species
in most cases had a spatial separation in biotope utilization.
2000 Academic Press
Keywords: fish; nursery grounds; bays; mangrove swamps; sea grasses; reefs; ontogenetic shifts; Caribbean Sea
Introduction
Many studies in various parts of the world have
recognized the importance of mangroves and seagrass
beds as habitats for fishes. Mangroves and seagrass
beds have been shown to contain a high diversity and
abundance of estuarine and/or coral reef fishes in the
Caribbean (e.g. Springer & McErlean, 1962; Austin,
1971; Weinstein & Heck, 1979; Thayer et al., 1987;
Baelde, 1990; Sedberry & Carter, 1993), in the Indian
Ocean (e.g. Little et al., 1988; van der Velde et al.,
1995; Pinto & Punchihewa, 1996), and in the Pacific
Ocean (e.g. Blaber, 1980; Bell et al., 1984; Robertson
& Duke, 1987; Blaber & Milton, 1990; Morton, 1990;
Tzeng & Wang, 1992).
Several hypotheses have been proposed to explain
the high abundance of (juvenile) fishes in mangroves
d
Corresponding author. E-mail: gerardv@sci.kun.nl
0272–7714/00/070031+14 $35.00/0
and seagrass beds. The hypotheses are based on
avoidance of predators, the abundance of food and
the interception of fish larvae: (a) the structural
complexity of these biotopes provide excellent
shelter against predators (Parrish, 1989; Robertson
& Blaber, 1992), (b) these biotopes are often located
at a distance from the coral reef or from off-shore
waters and are therefore less frequented by predators
(Shulman, 1985; Parrish, 1989), (c) the relatively
turbid water of the bays and estuaries decrease the
foraging efficiency of predators (Blaber & Blaber,
1980; Robertson & Blaber, 1992), (d) these biotopes
provide a great abundance of food for fishes (Odum
& Heald, 1972; Carr & Adams, 1973; Ogden &
Zieman, 1977) and (e) these biotopes often cover
extensive areas and may intercept planktonic fish
larvae more effectively than the coral reef (Parrish,
1989).
2000 Academic Press
32 I. Nagelkerken et al.
(a)
(b)
b
a
Gotomeer
6
0
5000 m
Klein Bonaire
a+b+c+d
5 d
4 a+b+c
VII
c
b
a
IV
I
II
0
1000 m
IX
III
Kralendijk
Lac
1 a+b
VIII
Sorobon
Cai
2 a+b
Dam
V
Pekelmeer
VI
3 a + b+ d
isles
mangroves
A. cervicornis
F 1. (a) Map of Bonaire showing the different coral reef study sites. a=20 to 25 m, b=10 to 15 m, c=3 to 5 m,
d=0 to 3 m. (b) Map of Lac Bay showing the different mangrove (II, IV, VI, VII, VIII, IX) and seagrass bed (I, III, V)
study sites. A. cervicornis=Acropora cervicornis.
Studies on fish community structure in Caribbean
lagoons, bays and estuaries containing mangroves or
seagrass beds often mention high densities of juvenile
fish and state that these biotopes function as nursery
areas for various coral reef fish species (e.g. Austin,
1971; Weinstein & Heck, 1979; Baelde, 1990;
Sedberry & Carter, 1993). In the Indo-Pacific,
however, the nursery function of these biotopes is
apparent only in some regions (Blaber, 1980; Bell
et al., 1984; Little et al., 1988; Tzeng & Wang, 1992),
whereas in other regions these biotopes do not appear
to be important (Quinn & Kojis, 1985; Thollot &
Kulbicki, 1988; Blaber & Milton, 1990; Thollot,
1992).
Most studies describing the nursery function of
mangroves and seagrass beds were based on qualitative observations, made no distinction between
abundances of juvenile and adult fishes, and did not
provide quantitative data on fish size. The few studies
which did provide size data for separate species only
mentioned the full size range of all fish caught
(Springer & McErlean, 1962; Austin, 1971). Hence,
size-frequency data of juvenile and adult reef fish are
largely lacking for these biotopes. Furthermore, many
fish species show ontogenetic shifts in habitat utilization and migrate from their nursery grounds to an
intermediate life stage habitat or to the coral reef
(Ogden & Ehrlich, 1977; Weinstein & Heck, 1979;
McFarland, 1980; Rooker & Dennis, 1991). The size
range and the biotopes where these shifts occur have
also not been described accurately for many fish
species.
Studies referring to the nursery function of lagoons,
bays and estuaries in the Caribbean have mostly
focused on either mangroves or seagrass beds, and
usually with a different sampling method. This makes
a comparison between studies and biotopes difficult.
Only a few studies have sampled both biotopes simultaneously (Thayer et al., 1987; Sedberry & Carter,
1993), and even fewer have included censuses on the
adjacent or off-shore coral reef (e.g. van der Velde
et al., 1992). Hence, quantitative data describing the
ecological links of fish faunas between mangroves,
seagrass beds and coral reefs are largely lacking
(Ogden & Gladfelter, 1983; Birkeland, 1985; Parrish,
1989).
To provide a better insight into the importance of
mangroves, seagrass beds and depth zones of the coral
reef as nursery biotopes and their interrelationship in
fish fauna, size frequency data were collected for
16 commercially important reef fish species in each
biotope, using a visual census technique. The objectives of the present study were to answer the following
four questions: (1) Which biotopes are used as a
nursery by the selected fish species? (2) Which biotope
is preferred by a fish species in case multiple nursery
biotopes are used? (3) Do fish species show an ontogenetic shift from their nursery biotopes to other
biotopes when reaching a larger size? (4) Do closely
related fish species show a spatial separation in
biotope utilization?
Materials and methods
Lac Bay is the largest bay of Bonaire with an area of
approximately 8 km2 and is situated on the exposed
eastern side of the island [Figure 1(a)]. The bay
Nursery function of mangroves, seagrass beds and the shallow coral reef 33
T 1. Depth, temperature and salinity of the seawater in
the six different biotopes
Seagrass bed
Mangroves
Coral reef
Coral reef
Coral reef
Coral reef
Depth (m)
Temperature (C)
Salinity
0·4–1·4
0·3–1·2
0–3
3–5
10–15
20–25
28·6–33·4
28·5–34·0
29·0–29·8
27·1–29·3
27·1–29·8
26·8–29·5
37–44
39–44
n.d.
n.d.
n.d.
n.d.
n.d.=no data.
consists of a shallow basin (0 to 3 m deep) and is
protected from wave exposure by a shallow barrier of
dead and living corals [Figure 1(b)]. The bay is
connected to the sea by a narrow channel which is
about 8 m deep. The soft-bottom flora of the bay
is dominated by the seagrass Thalassia testudinum and
the calcareous alga Halimeda opuntia. Other common
vegetation consists of the seagrass Syringodium
filiforme and the alga Avrainvillea nigricans. The bay
is bordered almost completely by the mangrove
Rhizophora mangle. In front of the bay the coral
reef is situated, which runs around the island. The
reef consists of a shallow reef terrace which sharply
drops off at an angle of 45 to 60 at a depth of
8 to 12 m.
The maximum tidal range on Bonaire is 30 cm (van
Moorsel & Meijer, 1993). The seagrass beds and
mangrove prop-roots at the study sites were not
exposed at low tide and ranged in depth from 0·3 to
1·4 m (Table 1). The temperature, measured during
the entire study period, ranged from 28·5 to 34·0 C
in the bay, and was on average higher than on of the
coral reef where it ranged from 26·8 to 29·8 C. The
salinity, measured at the beginning and at the end of
the study period, ranged from 37 to 44 in the seagrass
beds and from 39 to 44 in the mangroves. The water
of the bay is quite clear and horizontal Secchi visibility
ranges from 4·6 to 21·6 m in the central parts of the
bay (van Moorsel & Meijer, 1993).
Sixteen reef fish species were selected in the present
study. Species were selected which were abundant,
not too shy, easy to identify in the field and had a
non-cryptic life style. Further selection was on
basis of their economic value (i.e. reef fisheries,
aquarium fisheries, attraction for diving industry).
The 16 species consisted of five species of grunts
(Haemulidae): French grunt Haemulon flavolineatum,
bluestriped grunt H. sciurus, smallmouth grunt H.
chrysargyreum, Caesar grunt H. carbonarium, and
black margate Anisotremus surinamensis; four species of
snappers (Lutjanidae): yellowtail snapper Ocyurus
chrysurus, mahogany snapper Lutjanus mahogoni,
schoolmaster L. apodus, and gray snapper L. griseus;
three species of surgeonfishes (Acanthuridae): doctorfish Acanthurus chirurgus, ocean surgeon A. bahianus,
and blue tang A. coeruleus; one species of barracuda
(Sphyraenidae): great barracuda Sphyraena barracuda;
one species of parrotfish (Scaridae): stoplight
parrotfish Sparisoma viride; one species of damselfish
(Pomacentridae): sergeant major Abudefduf saxatilis;
and one species of butterflyfish (Chaetodontidae):
foureye butterflyfish Chaetodon capistratus.
The selected fish species were studied using a
visual census technique in six different biotopes, viz.
mangrove prop-roots and seagrass beds, and the
coral reef of 0 to 3 m, 3 to 5 m, 10 to 15 m and 15
to 20 m [Figure 1(a,b)]. Water clarity for visual
censuses was good in all six biotopes, even in the
mangroves. The visual census technique was based
on best estimation by eye of abundance and body
length of the selected fish species in permanent belt
transects in all six biotopes. Size classes of 5 cm were
used for the estimation of body length (TL). The
usage of smaller size classes was avoided to reduce
differences in size class estimation between observers. For the large-sized Sphyraena barracuda size
classes of 15 cm were used. Length estimation was
practiced prior to the censuses on objects with
known length lying on the sea bottom. In addition,
the underwater slates for data recording were
marked with a ruler for guidance in size estimation.
Visual census estimations of fish abundance were
compared with catches at two seagrass sites using the
drop net quadrat method (Hellier, 1958). At sites
VIII and IX [see Figure 1(b)] a drop net of
1010 m was installed on the seagrass bed. During
the morning (09.00–10.00h) the net was lowered
onto the sea bottom and all fishes within the net
were caught, identified and counted. A total of seven
drop net catches were made at the two seagrass sites
during August to December 1981. In addition, differences in estimation of abundance was statistically
tested (t-test) between the two observers for each
species in each biotope (96 cases).
Advantages of visual censuses are that they are
rapid, non-destructive, inexpensive, can be used for all
selected biotopes of this study, the same areas can be
resurveyed through time, and the results can be compared with many other studies (English et al., 1994).
Disadvantages are the differences in accuracy in estimation of numbers and sizes by the observers, and
fishes may be attracted or scared off by the observers
(English et al., 1994; Cheal & Thompson, 1997;
Thompson & Mapstone, 1997).
34 I. Nagelkerken et al.
T 2. Mean density (1000 m 2) of the 16 fish species in the six different biotopes surveyed by visual census, and mean
density on the seagrass beds based on drop net catches
Seagrass bed
Haemulon flavolineatum
H. sciurus
H. chrysargyreum
H. carbonarium
Anisotremus surinamensis
Ocyurus chrysurus
Lutjanus mahogoni
L. apodus
L. griseus
Acanthurus chirurgus
A. bahianus
A. coeruleus
Sphyraena barracuda
Sparisoma viride
Abudefduf saxatilis
Chaetodon capistratus
drop net
visual census
Mangroves
Coral reef
0–3 m
Coral reef
3–5 m
Coral reef
10–15 m
Coral reef
20–25 m
782·5
12·7
0·0
0·0
0·0
20·6
0·0
30·2
4·8
0·0
27·0
0·0
6·3
60·3
0·0
12·7
115·3
5·5
0·01
0·0
0·0
16·4
1·1
8·1
8·7
9·2
3·3
1·1
0·9
26·1
0·2
4·9
59·9
4·3
0·0
0·0
0·0
1·2
0·0
65·8
29·9
0·8
0·2
2·6
5·1
1·4
3·9
16·7
52·4
0·4
64·7
0·0
0·0
0·0
9·6
0·5
0·0
5·6
86·6
10·2
0·0
11·1
65·2
2·7
37·4
0·4
53·9
0·0
0·0
1·1
1·7
0·0
0·0
0·1
19·3
21·8
0·0
34·6
0·3
14·4
12·4
9·6
0·0
5·4
0·8
24·7
12·6
9·7
0·0
0·6
5·6
7·7
0·1
11·4
16·8
23·1
2·9
0·5
0·0
0·1
0·1
11·8
2·3
3·4
0·04
0·8
4·4
4·5
0·2
6·3
0·1
9·6
In each of the six biotopes, permanently marked
belt transects were established. In the seagrass beds,
a transect of 3003 m was established at three
different sites. In the mangroves, nine transects were
established of 3 m wide and 25 to 100 m long. On the
coral reef, six sites were selected and at each site,
transects of 3100 m were established at two to four
depth zones [Figure 1(a)]. During May to November
1981, visual censuses were done by two trained
observers together in the morning (09.00–11.00h) and
in the afternoon (14.00–16.00h) by means of
snorkelling or SCUBA diving. The census in each
transect was repeated at monthly intervals. The
fish counts in transects at the different sites, of the
morning and afternoon survey, and of all seven
months were pooled and averaged per area. They are
expressed as the average fish density per 1000 m2 for
each size class of each species in each biotope.
Cluster analyses were carried out using the computer programme CLUSTAN1C2 (Wishart, 1978).
The average-linkage method (Sokal & Michener,
1958) was used in combination with the Bray-Curtis
coefficient. Separate analyses were carried out for
closely related species belonging to a single family
(Haemulidae, Lutjanidae, Acanthuridae) using logtransformed data of the densities in the different size
classes and biotopes. Cluster analysis of all species
together was carried out on data in which densities
per size class for each biotope were transformed to
percentages of total composition of a particular
species. This was done to compare biotope utilization
between species without the data being affected by
differences in total fish densities.
Results
Drop net catches vs visual census
Catches with the drop net showed higher abundances
for some fish species than estimations with the
visual census technique (Table 2), especially for H.
flavolineatum. On the other hand, visual estimations of
abundance of A. chirurgus were much higher than with
the drop net quadrat method. For the visual censuses,
only in 8 out of 61 cases a significant difference
(P<0·05, t-test) was found in estimation of abundance
between the two observers (for 35 cases insufficient
data were available for statistical testing).
Biotope utilization of Haemulidae
Juveniles of Haemulidae were restricted to shallow
water biotopes (i.e. seagrass beds, mangroves and reef
of 0 to 3 m), whereas adults were found on the deeper
reef (>3 m) (Figure 2, Table 3). An exception was
formed by adult Haemulon chrysargyreum which were
also found on the reef of 0 to 3 m. Large juveniles of
H. sciurus utilized the mangroves as an intermediate
life stage biotope, in their ontogenetic shift from the
seagrass beds to the coral reef. Haemulon flavolineatum
showed significant temporal differences in total
density in the seagrass beds (Friedman’s test,
Nursery function of mangroves, seagrass beds and the shallow coral reef 35
(a)
Coral reef 20–25 m
Coral reef 10–15 m
Coral reef 3–5 m
Coral reef 0–3 m
Seagrass bed
Mangroves
100
80
60
40
20
0
0–5
5–10
10–15
Size class (cm)
15–20
8
Summed mean density
(1000 m–2)
Summed mean density
(1000 m–2)
120
20–25
6
5
4
3
2
1
5–10
10–15 15–20 20–25
Size class (cm)
25–30
30–35
5–10
10–15 15–20 20–25
Size class (cm)
25–30
30–35
4
(c)
Summed mean density
(1000 m–2)
Summed mean density
(1000 m–2)
(b)
0
0–5
60
50
7
40
30
20
10
0
0–5
5–10
10–15
Size class (cm)
15–20
20–25
(d)
3
2
1
0
0–5
Summed mean density
(1000 m–2)
0.5
(e)
0.4
0.3
0.2
0.1
0.0
0–5
5–10 10–15 15–20 20–25 25–30 30–35 35–40
Size class (cm)
F 2. Summed mean densities of Haemulidae in different biotopes. (a) Haemulon flavolineatum; (b) H. sciurus;
(c) H. chrysargyreum; (d) H. carbonarium; (e) Anisotremus surinamensis.
P<0·05), increasing from 25·4 per 1000 m2 in May to
178·9 per 1000 m2 in October.
Cluster analysis of all size classes of all haemulids
also showed a spatial separation in biotope utilization
among the different size classes and/or species, with
juveniles found in the mangroves and seagrass beds,
medium-sized individuals on the reef and partly still in
the mangroves, and very large individuals on the deep
reef (Figure 3). Haemulon chrysargyreum formed a
separate cluster since adults partly co-occurred with
the juveniles in their nursery habitat.
Species of Haemulidae showed a spatial separation
in biotope utilization and occurred in different biotope
clusters as calculated by cluster analysis (Figure 4).
Furthermore, the Haemulidae were not found
together in a single cluster with any species belonging
to the same feeding guild (Figure 4, Table 3). Only
H. carbonarium and A. surinamensis showed some
similarity in biotope utilization, but the former was
much more abundant than the latter (Figure 2).
Considering the entire species size range, H.
flavolineatum dominated over its related species in the
seagrass beds, mangroves and reef of 20 to 25 m, but
co-occurred with H. chrysargyreum on the reef of 0 to
5 m [Figure 5(a), Table 2]. Haemulon sciurus and
H. carbonarium co-occurred with H. flavolineatum on
the reef of 10 to 15 m. Anisotremus surinamensis was
not dominant in any of the biotopes.
Biotope utilization of Lutjanidae
Juveniles of Lutjanidae were restricted to the shallow
water biotopes (Figure 6, Table 3). Only juveniles of
L. mahogoni were also partly found deeper on the reef
36 I. Nagelkerken et al.
T 3. Importance (+) of the six different biotopes for juveniles and adults of the different fish species. *Indicates most important biotope for juveniles. Maturation
size refers to that of the smallest individuals and not to the species average. Maturation data are from De Sylva (1963), Starck and Schroeder (1971); Munro (1983).
Ontogenetic migration indicates the migration of juveniles to the (deeper) coral reef when reaching adult sizes; +/ = partial ontogenetic migration (i.e. part of the
fish population). Feeding guilds: BI=benthic invertebrate feeder, PI=planktonic invertebrate feeder, P=piscivore, H=herbivore, O=omnivore. Ontogenetic shifts in
feeding guild are indicated as that of juveniles/adults
Feeding
guild
Haemulon flavolineatum
H. sciurus
H. chrysargyreum
H. carbonarium
Anisotremus surinamensis
Ocyurus chrysurus
Lutjanus mahogoni
L. apodus
L. griseus
Acanthurus chirurgus
A. bahianus
A. coeruleus
Sphyraena barracuda
Sparisoma viride
Abudefduf saxatilis
Chaetodon capistratus
BI
BI
BI
BI
BI
PI
BI/P
BI/P
BI/P
H
H
H
P
H
O
H/BI
Juveniles
Adults
Maturation
size
Seagrass
Reef
Reef
Reef
Reef
Seagrass
Reef
Reef
Reef
Reef
Ontogenetic
(cm)
bed
Mangroves 0–3 m 3–5 m 10–15 m 20–25 m
bed
Mangroves 0–3 m 3–5 m 10–15 m 20–25 m migration
>10
>15
>15
>15
>20
>25
>20
>25
>15
>15
>10
>10
>45
>15
>10
>5
+*
+*
+
+
+
+
+*
+*
+
+
+
+*
+
+
+
+*
+*
+
+*
+
+
+
+*
+
+
+
+
+
+
+
+*
+
+
+*
+*
+*
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+
+/
?
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+
+
+
+/
+/
+/
+/
+/
+/
+
Nursery function of mangroves, seagrass beds and the shallow coral reef 37
0.9
0.8
Dissimilarity
0.7
0.6
0.5
0.4
0.3
0.2
Seagrass and mangrove Coral reef and mangrove
Shallow reef
Seagrass
A. su. 20–25
H. ca. 30–35
A. su. 30–35
A. su. 35–40
A. su. 25–30
H. ca. 15–20
H. ca. 20–25
H. ca. 25–30
H. sc. 30–35
H. sc. 0–5
H. ch.20–25
H. ch. 15–20
H. ch. 10–15
H. ch. 5–10
H. ch. 0–5
H. sc. 20–25
H. sc. 15–20
H. sc. 25–30
H. fl. 20–25
H. fl. 15–20
H. fl. 10–15
H. sc. 10–15
H. sc. 5–10
H. fl. 5–10
0.0
H. fl. 0–5
0.1
Deep reef
F 3. Cluster analysis of all size classes of Haemulidae in different biotopes. H. fl.=Haemulon flavolineatum,
H. sc.=H. sciurus, H. ch.=H. chrysargyreum, H. ca.=H. carbonarium, A. su.=Anisotremus surinamensis. The numbers indicate
the size classes.
0.9
0.8
Dissimilarity
0.7
0.6
0.5
0.4
0.3
0.2
3
6
7
8
L. apodus
L. griseus
A. surinamensis
H. carbonarium
L. mahogoni
5
O. chrysurus
4
H. sciurus
C. capistratus
S. viride
A. coeruleus
A. bahianus
2
A. saxatilis
1
H. chrysargyreum
A. chirurgus
0.0
H. flavolineatum
0.1
9
F 4. Cluster analysis of all 16 fish species based on the abundance of each size class in the different biotopes.
of 3 to 5 m. All species, except L. griseus, showed an
ontogenetic shift to the (deeper) coral reef. Lutjanus
apodus and L. griseus also occurred as adults in the
mangroves. Lutjanus apodus showed significant temporal differences in total density (Friedman’s test,
P<0·05), increasing in the mangroves from 57·7 per
1000 m2 in May to 92·3 per 1000 m2 in August, and
in the seagrass beds from 0·9 per 1000 m2 in May
to 17·2 per 1000 m2 in October. Ocyurus chrysurus
increased in density in the seagrass beds from 4·4 per
1000 m2 in June to 41·4 per 1000 m2 in November.
Cluster analysis of all size classes of all lutjanids also
revealed a clear separation between adults and large
individuals (except L. griseus) on the deep reef (10 to
38 I. Nagelkerken et al.
(a)
100%
80%
60%
40%
20%
0%
H. sciurus
H. carbonarium
H. flavolineatum
H. chrysargyreum
A. surinamensis
(b)
100%
Biotope utilization of Acanthuridae
80%
Composition
60%
40%
20%
0%
O. chrysurus
L. griseus
L. mahogoni
L. apodus
(c)
100%
80%
60%
40%
20%
A. bahianus
A. chirurgus
m
25
m
ee
R
f1
f2
0–
0–
15
m
ee
R
R
ee
f
0–
3
ee
f
R
3–
5
es
gr
ov
s
M
an
a
be gra
d s
m
0%
Se
25 m), and juveniles in the shallow water biotopes
(Figure 7).
Species of Lutjanidae showed a spatial separation in
biotope utilization, except L. griseus and L. apodus
which showed some degree of similarity in biotope
utilization and also belonged to the same feeding guild
(Figure 4, Table 3). Considering the entire species
size range, L. apodus dominated over its related
species in the mangroves, while for L. mahogoni
and O. chrysurus this was the case on the reef of 0
to 3 m and on the reef of 20 to 25 m, respectively
[Figure 5(b), Table 2]. In the other three biotopes,
lutjanids co-occurred without a single species showing
an overall dominance.
A. coeruleus
F 5. Biotope partitioning between closely related
species: (a) Haemulidae, (b) Lutjanidae, (c) Acanthuridae.
The abundance of each species is expressed as the percentage composition of the total abundance of all related species
within a single family for each biotope. The entire size range
of a species is pooled per biotope, although preferences may
differ among size classes. For the specific differences among
size classes see Figures 2, 6 and 8.
Juveniles of Acanthuridae were restricted to the
shallow water biotopes, whereas adults were found on
the reef (Figure 8, Table 3). Adults were also found in
the juvenile nursery habitat (i.e. reef of 0 to 3 m),
however, co-occurring with the juveniles. For larger
juveniles of A. coeruleus the reef of 3 to 5 m was also of
importance. Acanthurus bahianus showed significant
temporal differences in total density (Friedman’s
test, P<0·05), with peak abundances in the seagrass
beds of around 5 per 1000 m2 in July, October, and
November. Acanthurus coeruleus increased in density
on the reef of 3 to 5 m from 5·4 per 1000 m2 in May
to 47·1 per 1000 m2 in September.
Cluster analysis of all size classes of all acanthurids
also showed a separation between juveniles in the
seagrass beds and mangroves, and medium-sized and
larger individuals on the reef (Figure 9).
Species of Acanthuridae showed a spatial separation
in biotope utilization and occurred in different biotope
clusters (Figure 4). Of the Acanthuridae, only A.
coeruleus was found with another herbivore species
(S. viride) in a single cluster, although the dissimilarity
in biotope utilization between the two species was still
high (Figure 4, Table 3). Considering the entire
species size range, each species dominated over its
related species in a particular biotope: A. chirurgus in
the seagrass beds, A. coeruleus in the mangroves, and
A. bahianus on the coral reef of 0 to 3 m [Figure 5(c),
Table 2). In the other reef zones, A. coeruleus and
A. bahianus co-occurred in almost equal densities.
Biotope utilization of other species
For the remaining four species, juveniles were also
restricted to the shallow water biotopes, whereas
adults occurred on the coral reef (Figures 10–13,
Table 3). Exceptions were adult S. barracuda which
Nursery function of mangroves, seagrass beds and the shallow coral reef 39
(a)
15
Mangroves
Coral reef 0–3 m
Coral reef 10–15 m
Seagrass bed
Coral reef 3–5 m
Coral reef 20–25 m
10
5
0
0–5
7
Summed mean density
(1000 m–2)
Summed mean density
(1000 m–2)
20
(b)
5
4
3
2
1
0
0–5
5–10 10–15 15–20 20–25 25–30 30–35 35–40
Size class (cm)
25
5–10
10–15 15–20 20–25
Size class (cm)
25–30
30–35
14
(c)
Summed mean density
(1000 m–2)
Summed mean density
(1000 m–2)
6
20
15
10
5
0
0–5
5–10 10–15 15–20 20–25 25–30 30–35 35–40 40–45
12
(d)
10
8
6
4
2
0
0–5 5–10 10–15 15–20 20–25 25–30 30–35 35–40 40–45 45–50
Size class (cm)
Size class (cm)
Bay and shallow reef
L. ap. 40–45
L. ma. 30–35
L. ma. 15–20
O. ch. 30–35
O. ch. 20–25
O. ch. 25–30
an
R d0
ee
–
f1 3m
0–
25
m
R
ee
f1
0–
25
m
L. ma. 20–25
L. ma. 25–30
L. ap. 35–40
O. ch. 35–40
O. ch. 15–20
R
ee
f1
0–
25
L. ap. 25–30
L. ap. 30–35
L. ma. 0–5
L. ma. 5–10
L. ma. 10–15
L. gr. 40–45
L. gr. 45–50
O. ch. 0–5
O. ch. 5–10
O. ch. 10–15
L. ap . 0–5
L. ap. 15–20
L. ap. 20–25
M
re ang
ef ro
10 ve
–1 an
5 d
m
Se
ag
ra
ss
M
an
gr
ov
e
R
ee
f0
–5
m
L. ap. 5–10
L. ap. 10–15
L. gr. 20–25
L. gr. 25–30
se
ag
ra
ss
L.gr. 5–10
L.gr. 10–15
L. gr. 15–20
M
an
gr
ov
e
an
d
L. gr. 0–5
L. gr. 35–40
L. gr. 30–35
0.9
0.8
0.7
0.6
0.5
0.4
0.3
0.2
0.1
0.0
M
an
gr
ov
e
Dissimilarity
F 6. Summed mean densities of Lutjanidae in different biotopes. (a) Ocyurus chrysurus; (b) Lutjanus mahogoni;
(c) L. apodus; (d) L. griseus.
Deep reef
F 7. Cluster analysis of all size classes of Lutjanidae in different biotopes. L. gr.=Lutjanus griseus, L. ap.=L. apodus,
L. ma.=L. mahogoni, O. ch.=Ocyurus chrysurus. The numbers indicate the size classes.
also used the seagrass beds and mangroves as a life
stage biotope, and juvenile S. viride which also used
the reef of 3 to 5 m as a nursery biotope. Some adult
A. saxatilis co-occurred with the juveniles on the
shallow reef. Sphyraena barracuda showed significant
temporal differences in total density (Friedman’s test,
40 I. Nagelkerken et al.
Coral reef 20–25 m
Coral reef 10–15 m
Coral reef 3–5 m
Coral reef 0–3 m
Seagrass bed
Mangroves
(a)
8
6
4
2
0
0–5
5–10
10–15
15–20
Size class (cm)
20–25
50
Summed mean density
(1000 m–2)
Summed mean density
(1000 m–2)
10
(b)
40
30
20
10
0
0–5
25–30
5–10
10–15
15–20
Size class (cm)
20–25
25–30
Summed mean density
(1000 m–2)
20
(c)
16
12
8
4
0
0–5
5–10
10–15
Size class (cm)
15–20
20–25
F 8. Summed mean densities of Acanthuridae in different biotopes. (a) Acanthurus chirurgus; (b) A. bahianus;
(c) A. coeruleus.
1.0
0.9
0.8
Dissimilarity
0.7
0.6
0.5
0.4
0.3
0.2
Seagrass and reef
0–3 m
Reef 0–25 m
Reef and bay
A. ch. 25–30
A. ba. 25–30
A. ch. 20–25
A. ch. 15–20
A. co. 5–10
A. co. 0–5
A. ch. 10–15
A. co. 20–25
A. ba. 20–25
A. co. 15–20
A. ba. 15–20
A. co. 10–15
A. ba 10–15
A. ch. 5–10
A. ch. 0–5
A. ba. 5–10
0.0
A. ba 0–5
0.1
Reef
0–25 m
F 9. Cluster analysis of all size classes of Acanthuridae in different biotopes. A. ba.=Acanthurus bahianus,
A. ch.=A. chirurgus, A. co.=A. coeruleus. The numbers indicate the size classes.
P<0·05), with densities in the mangroves about two
times higher in August–November than in May–July.
Sparisoma viride increased in density in the seagrass
beds from 12·7 per 1000 m2 in June to 43·1 per
1000 m2 in November, and C. capistratus from 2·0 per
1000 m2 in May to 8·0 per 1000 m2 in November.
Coral reef 20–25 m
Coral reef 10–15 m
Coral reef 3–5 m
Coral reef 0–3 m
Seagrass bed
Mangroves
2
195–210
180–195
165–180
150–165
135–150
105–120
120–135
90–105
75–90
60–75
45–60
30–45
0
0–15
1
15–30
Summed mean density
(1000 m–2)
3
Size class (cm)
F 10. Summed mean densities of Sphyraena barracuda
in different biotopes.
Summed mean density
(1000 m–2)
30
Coral reef 20–25 m
Coral reef 10–15 m
Coral reef 3–5 m
Coral reef 0–3 m
Seagrass bed
Mangroves
25
20
15
10
5
0
0–5
5–10 10–15 15–20 20–25 25–30 30–35 35–40
Size class (cm)
F 11. Summed mean densities of Sparisoma viride in
different biotopes.
Summed mean density
(1000 m–2)
60
Coral reef 20–25 m
Coral reef 10–15 m
Coral reef 3–5 m
Coral reef 0–3 m
Seagrass bed
Mangroves
50
40
30
20
10
0
0–5
5–10
10–15
Size class (cm)
15–20
20–25
F 12. Summed mean densities of Abudefduf saxatilis in
different biotopes.
Discussion
For several fish species in the seagrass beds the visual
census technique showed lower densities than the
catches with the drop net quadrat method. Especially
H. flavolineatum was underestimated in the visual
censuses. The formation of large schools in this and
other species and the continuous movement of the
fishes caused a reduced accuracy in the estimation
Summed mean density
(1000 m–2)
Nursery function of mangroves, seagrass beds and the shallow coral reef 41
Coral reef 20–25 m
Coral reef 10–15 m
Coral reef 3–5 m
Coral reef 0–3 m
Seagrass bed
Mangroves
60
50
40
30
20
10
0
0–5
5–10
Size class (cm)
F 13. Summed mean
capistratus in different biotopes.
densities
10–15
of
Chaetodon
of fish abundance. This variation is assumed to be
comparable for the different biotopes, making a comparison among the biotopes possible. Differences in
estimation of abundance between observers were
present, but not consistent. Although density estimations in seagrass beds are more accurate with
the drop net quadrat method, the total surface area
sampled (100 m2) was much smaller than with the
visual censuses (900 m2), resulting in large variations
among the transects and a restricted sampling of the
biotope studied.
The present study shows the importance of
different shallow water biotopes as a nursery for
economically important reef fish species. All 14
species for which juveniles were observed used either
the mangroves, seagrass beds or the shallow reef of
0 to 3 m, or a combination of these biotopes, as a
nursery. The high dependence of juveniles on
these biotopes can be deduced from the fact that
juveniles were exclusively present or highly dominant
in these biotopes and not on the deeper reef (i.e.
>3 m).
The data show that not only mangroves and
seagrass beds are important nursery biotopes for
juvenile fishes (e.g. Austin, 1971; Weinstein & Heck,
1979; Baelde, 1990; Sedberry & Carter, 1993)
but also the shallow coral reef. Two reasons why
mangroves and seagrass beds may contain high
densities of juvenile fish is their structural complexity
which provides a hiding place against predators (Bell
& Westoby, 1986; Robertson & Blaber, 1992), and
because they are often located at a distance from
the coral reef and are therefore less frequented by
predators (Shulman, 1985; Parrish, 1989). These two
factors also apply to the shallow coral reef of Bonaire,
which mostly consists of living and dead colonies of
Acropora palmata, Millepora complanata and other
42 I. Nagelkerken et al.
corals. The dead and living corals provide an ideal
hiding space and can house relatively high densities of
(juvenile) fish (Nagelkerken, 1974). Furthermore, the
shallow reef is separated from the main coral reef and
its predators by a shallow reef terrace of about 75 to
125 m in width (van Duyl, 1985). Shulman (1985)
showed that at just 20 m from the main reef, in
an exposed sandy location, predation on juvenile
haemulids was considerably lower than at the edge of
the main reef.
Biotope utilization appears to be very specific for
the different species and their size classes, each having
a different niche. A clear spatial separation in biotope
utilization was found among closely related species
and among different size groups within species, suggesting avoidance of competition. Biotope partitioning
was observed for only a small size range of mostly one
or two related species. Likewise, fish species belonging to the same feeding guild showed differences in
biotope utilization. Spatial variation across different
biotopes often occurs among sympatric fish species
(Lewis & Wainwright, 1985; McAfee & Morgan,
1996). Comparable to the present study, Lewis and
Wainwright (1985) found a differential biotope
utilization for the three species of Acanthuridae and
suggested this to be determined by complex interactions of several factors, such as density of competitors, food availability, proximity to shelter, and
predator abundance. Munro (1983) stated that interspecific competition for food is probably small for
Haemulidae since the different species each favour a
certain type of food (Randall, 1967). Nagelkerken
et al. (2000), however, found H. flavolineatum and H.
sciurus to have similar diets on seagrass beds, which
may explain the separation in biotope utilization of the
different size classes. Lutjanidae show a high overlap
in diet, with exception of Ocyurus chrysurus (Randall,
1967; Nagelkerken et al., 2000). As biotope utilization differed only slightly between Lutjanus mahogoni
and L. griseus, which both occurred in similar
densities, a high degree of competition may be present
between these two species.
When fishes become too large for optimal protection
by the seagrass shoots and mangrove prop-roots they
often migrate to the coral reef. This migration pattern
has largely been described qualitatively for only few
species (e.g. Ogden & Ehrlich, 1977; Weinstein &
Heck, 1979; McFarland, 1980; Rooker & Dennis,
1991). The present study shows that most of the
selected species use the shallow water biotopes as nurseries during their juvenile stage, but migrate permanently to the (deeper) coral reef when reaching a
specific size class. An exception was Lutjanus griseus
of which the entire size range was found in the
mangroves. For some species, the ontogenetic shift to
the (deeper) coral reef was partial and a part of the
large and adult fish could still be found in their nursery
biotope.
The present study shows the importance of Lac Bay
for a number of reef fish species. It is not known,
however, how much Lac Bay contributes to the reef
fish stocks of Bonaire. Effective areas of all biotopes
should therefore be measured and the turnover rate
of fishes from the bay to the reef be quantified.
Furthermore, it should be noted that Lac Bay is not
comparable to many other mangrove and seagrass
habitats, particularly in the Indo-Pacific. These
habitats often have a muddy substratum, are very
turbid, and show fluctuating salinities and a greater
tidal range. These features influence the nursery
function of mangroves and seagrass beds (Blaber,
1997). As the characteristics which are usually associated with these habitats are reduced in Lac Bay, the
mechanisms at work responsible for the nursery
function of this bay may differ from those in several
other bays, lagoons and estuaries which have been
studied so far.
Conclusions
The questions asked in this study can be answered as
follows. (1) Of all 14 fish species for which juveniles
were observed, the mangroves, seagrass beds, shallow
reef of 0 to 3 m, or a combination of these biotopes
were used as a nursery by the juveniles. (2) The
seagrass beds were the most important nursery biotope
for juvenile Haemulon flavolineatum, H. sciurus,
Ocyurus chrysurus, Acanthurus chirurgus and Sparisoma
viride, the mangroves were the most important biotope
for juvenile Lutjanus apodus, L. griseus, Sphyraena
barracuda and Chaetodon capistratus, the shallow coral
reef was the most important biotope for juvenile H.
chrysargyreum, L. mahogoni, A. bahianus and Abudefduf
saxatilis, Acanthurus coeruleus did not show a preference for a particular nursery habitat, and for H.
carbonarium and Anisotremus surinamensis it could not
be established which biotope was used as a nursery by
the juveniles. (3) For most fish species, the juveniles
were found in shallow-water biotopes and the large
and adult fish on the (deeper) coral reef. (4) Closely
related species showed a spatial separation in biotope
utilization. This was also observed for different size
classes within species.
Acknowledgements
This study was funded by grants to MWG and
GJM from the Stichting Werkgroep Studiereizen
Nursery function of mangroves, seagrass beds and the shallow coral reef 43
Ontwikkelingslanden, the Beijerinck-Popping Fonds,
and the Natuurwetenschappelijke Studiekring voor
Suriname en de Nederlandse Antillen. We would
like to thank E. Newton of Stinapa Bonaire (Bonaire)
and the staff of the Carmabi Foundation (Curaçao)
for their co-operation. We furthermore thank
Dr M. de Kluijver for doing the CLUSTAN analyses
and Dr S. Rajagopal for his comments on the
manuscript.
References
Austin, H. M. 1971 A survey of the ichtyofauna of the mangroves of
western Puerto Rico during December, 1967–August, 1968.
Caribbean Journal of Science 11, 27–39.
Baelde, P. 1990 Differences in the structures of fish assemblages in
Thalassia testudinum beds in Guadeloupe, French West Indies,
and their ecological significance. Marine Biology 105, 163–173.
Bell, J. D. & Westoby, M. 1986 Abundance of macrofauna in dense
seagrass is due to habitat preference, not predation. Oecologia 68,
205–209.
Bell, J. D., Pollard, D. A., Burchmore, J. J., Pease, B. C. &
Middleton, M. J. 1984 Structure of a fish community in a
temperate tidal mangrove creek in Botany Bay, New South
Wales. Australian Journal of Marine and Freshwater Research 35,
33–46.
Birkeland, C. 1985 Ecological interactions between mangroves,
seagrass beds, and coral reefs. In Ecological Interactions Between
Tropical Coastal Ecosystems (Birkeland, C. & Grosenbaugh, D.,
eds). UNEP Regional Seas Reports and Studies No. 73, 1–26.
Blaber, S. J. M. 1980 Fish of the Trinity inlet system of north
Queensland with notes on the ecology of fish faunas of tropical
Indo-Pacific estuaries. Australian Journal of Marine and Freshwater
Research 31, 137–146.
Blaber, S. J. M. 1997 Fish and Fisheries of Tropical Estuaries.
Chapman and Hall, London.
Blaber, S. J. M. & Blaber, T. G. 1980 Factors affecting the
distribution of juvenile estuarine and inshore fish. Journal of Fish
Biology 17, 143–162.
Blaber, S. J. M. & Milton, D. A. 1990 Species composition,
community structure and zoogeography of fishes of mangrove
estuaries in the Solomon Islands. Marine Biology 105, 259–267.
Carr, W. E. S. & Adams, C. A. 1973 Food habits of juvenile marine
fishes occupying seagrass beds in the estuarine zone near Crystal
River, Florida. Transactions of the American Fisheries Society 102,
511–540.
Cheal, A. J. & Thompson, A. A. 1997 Comparing visual counts
of coral reef fish: implications of transect width and species
selection. Marine Ecology Progress Series 158, 241–248.
De Sylva, D. P. 1963 Systematics and life-history of the great
barracuda Sphyraena barracuda (Walbaum). Studies in Tropical
Oceanography 1, 179.
English, S., Wilkinson, C. & Baker, V. (eds) 1994 Survey Manual
for Tropical Marine Resources. ASEAN-Australia Marine
Science Project: Living Coastal Resources. Australian Institute
of Marine Science, Townsville, pp. 68–80.
Hellier, T. R. 1958 The drop-net quadrat, a new population
sampling device. Publications of the Institute for Marine Science of
the University of Texas 5, 165–168.
Lewis, S. M. & Wainwright, P. C. 1985 Herbivore abundance
and grazing intensity on a Caribbean coral reef. Journal of
Experimental Marine Biology and Ecology 87, 215–228.
Little, M. C., Reay, P. J. & Grove, S. J. 1988 The fish community
of an East African mangrove creek. Journal of Fish Biology 32,
729–747.
McAfee, S. T. & Morgan, S. G. 1996 Resource use by five
sympatric parrotfishes in the San Blas Archipelago, Panama.
Marine Biology 125, 427–437.
McFarland, W. N. 1980 Observations on recruitment in haemulid
fishes. Proceedings of the Gulf and Caribbean Fisheries Institute 32,
132–138.
Morton, R. M. 1990 Community structure, density and standing
crop of fishes in a subtropical Australian mangrove area. Marine
Biology 105, 385–394.
Munro, J. L. 1983 Caribbean coral reef fishery resources. ICLARM
studies and reviews 7.
Nagelkerken, W. P. 1974 On the occurrence of fishes in relation to
corals in Curaçao. Studies on the Fauna of Curaçao and other
Caribbean Islands 45, 118–141.
Nagelkerken, I., Dorenbosch, M., Verberk, W. C. E. P., Cocheret
de la Morinière, E. & van der Velde, G. 2000 Day-night shifts
of fishes between shallow-water biotopes of a Caribbean bay,
with emphasis on the nocturnal feeding of Haemulidae and
Lutjanidae. Marine Ecology Progress Series 194, 55–64.
Odum, W. E. & Heald, E. J. 1972 Trophic analyses of an estuarine
mangrove community. Bulletin of Marine Science 22, 671–738.
Ogden, J. C. & Ehrlich, P. R. 1977 The behavior of heterotypic
resting schools of juvenile grunts (Pomadasyidae). Marine Biology
42, 273–280.
Ogden, J. C. & Gladfelter, E. H. (eds) 1983 Coral reefs, seagrass
beds, and mangroves: their interaction in the coastal zones of the
Caribbean. UNESCO Reports in Marine Science 23, 133 pp.
Ogden, J. C. & Zieman, J. C. 1977 Ecological aspects of coral
reef-seagrass bed contacts in the Caribbean. Proceedings of the
Third International Coral Reef Symposium 1, 377–382.
Parrish, J. D. 1989 Fish communities of interacting shallow-water
habitats in tropical oceanic regions. Marine Ecology Progress Series
58, 143–160.
Pinto, L. & Punchihewa, N. N. 1996 Utilisation of mangroves and
seagrasses by fishes in the Negombo Estuary, Sri Lanka. Marine
Biology 126, 333–345.
Quinn, N. J. & Kojis, B. J. 1985 Does the presence of coral reefs
in proximity to a tropical estuary affect the estuarine fish
assemblage? Proceedings of the Fifth International Coral Reef
Congress 5, 445–450.
Randall, J. E. 1967 Food habits of reef fishes in the West Indies.
Studies in Tropical Oceanography 5, 665–847.
Robertson, A. I. & Blaber, S. J. M. 1992 Plankton, epibenthos and
fish communities. In Tropical Mangrove Ecosystems (Robertson,
A. I. & Alongi, D. M., eds). Coastal and Estuarine Studies
No. 41, 173–224.
Robertson, A. I. & Duke, N. C. 1987 Mangroves as nursery sites:
comparisons of the abundance and species composition of fish
and crustaceans in mangroves and other nearshore habitats in
tropical Australia. Marine Biology 96, 193–205.
Rooker, J. R. & Dennis, G. D. 1991 Diel, lunar and seasonal
changes in a mangrove fish assemblage off southwestern Puerto
Rico. Bulletin of Marine Science 49, 684–698.
Sedberry, G. R. & Carter, J. 1993 The fish community of a shallow
tropical lagoon in Belize, Central America. Estuaries 16, 198–215.
Shulman, M. J. 1985 Recruitment of coral reef fishes: effects of
distribution of predators and shelter. Ecology 66, 1056–1066.
Sokal, R. R. & Michener, C. D. 1958 A statistical method for
evaluating systematic relationships. Kansas University Science
Bulletin 38, 1409–1438.
Springer, V. G. & McErlean, A. J. 1962 Seasonality of fishes on a
south Florida shore. Bulletin of Marine Science of the Gulf and
Caribbean 12, 39–60.
Starck, W. A. & Schroeder, R. E. 1971 Investigations on the gray
snapper, Lutjanus griseus. Studies in Tropical Oceanography 10.
Thayer, G. W., Colby, D. R. & Hettler, W. F. 1987 Utilization of
the red mangrove prop root habitat by fishes in south Florida.
Marine Ecology Progress Series 35, 25–38.
Thollot, P. 1992 Importance of mangroves for Pacific reef fish
species, myth or reality? Proceedings of the Seventh International
Coral Reef Symposium 2, 934–941.
44 I. Nagelkerken et al.
Thollot, P. & Kulbicki, M. 1988 Overlap between the fish fauna
inventories of coral reefs, soft bottoms and mangroves in
Saint-Vincent Bay (New Caledonia). Proceedings of the Sixth
International Coral Reef Symposium 2, 613–618.
Thompson, A. A. & Mapstone, B. D. 1997 Observer effects and
training in underwater visual surveys of reef fishes. Marine Ecology
Progress Series 154, 53–63.
Tzeng, W.-N. & Wang, Y.-T. 1992 Structure, composition and
seasonal dynamics of the larval and juvenile fish community in
the mangrove estuary of Tanshui River, Taiwan. Marine Biology
113, 481–490.
van der Velde, G., Gorissen, M. W., den Hartog, C., van’t Hof, T.
& Meijer, G. J. 1992 Importance of the Lac-lagoon (Bonaire,
Netherlands Antilles) for a selected number of reef fish species.
Hydrobiologia 247, 139–140.
van der Velde, G., van Avesaath, P. H., Ntiba, M. J., Mwatha,
G. K., Marguillier, S. & Woitchik, A.-F. 1995 Fish fauna of
mangrove creeks, seagrass meadows and sand flats in Gazi Bay,
Kenya (Indian Ocean): a study with nets and stable isotopes. In
Monsoons and Coastal Ecosystems in Kenya (Heip, C. H. R.,
Hemminga, M. A. & de Bie, M. J. M., eds). Netherlands Indian
Ocean Programme Cruise Reports No. 5, 39–50.
van Duyl, F. C. 1985 Atlas of the living reefs of Curaçao and Bonaire
(Netherlands Antilles). Foundation for scientific research in
Surinam and the Netherlands Antilles, no. 117, Utrecht,
The Netherlands.
van Moorsel, G. W. N. M. & Meijer, A. J. M. 1993 Base-line
Ecological Study van het Lac op Bonaire. Bureau Waardenburg bv,
Culemborg, The Netherlands.
Weinstein, M. P. & Heck, K. L. 1979 Ichtyofauna of seagrass
meadows along the Caribbean coast of Panamá and in the gulf of
Mexico: composition, structure and community ecology. Marine
Biology 50, 97–107.
Wishart, D. 1978 CLUSTAN User Manual. Programme Library
Unit, Edinburgh University, Edinburgh.