Role of Demersal Zooplankton as a Food Source for Higher Trophic Levels at Fukido Estuary, Ishigaki Island, Okinawa, Japan  

Hung Manh Vu1,2 , Beatriz Estela Casareto1,3 , Ken-ichi Hayashizaki4 , Laddawan Sangsawang1,5 , Keita Toyoda3 , Lan Dinh Tran2 , Yoshimi Suzuki1
1 Graduate School of Science and Technology, Shizuoka University, 836 Ohya, Suruga-ku, Shizuoka-Shi, Shizuoka-Ken 422-8529, Japan
2 Institute of Marine Environment and Resources, Vietnam Academy of Science and Technology (VAST), 246 Danang Street, Haiphong City 180000, Vietnam
3 Research Institute of Green Science and Technology, Shizuoka University, 836 Ohya, Suruga-ku, Shizuoka-Shi, Shizuoka-Ken 422-8529, Japan
4 School of Marine Biosciences, Kitasato University, Kitasato, Minami-ku, Sagamihara, Kanagawa 252-0373, Japan
5 Marine and Coastal Resources Research and Development Center the eastern Gulf of Thailand, Pak Nam Prasae, Klaeng, Rayong Province 21170, Thailand
Author    Correspondence author
International Journal of Marine Science, 2017, Vol. 7, No. 17   doi: 10.5376/ijms.2017.07.0017
Received: 11 Apr., 2017    Accepted: 10 May, 2017    Published: 23 May, 2017
© 2017 BioPublisher Publishing Platform
This is an open access article published under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.
Preferred citation for this article:

Vu H.M., Casareto B.E., Hayashizaki K.I., Sangsawang L., Toyoda K., Tran L.D., and Suzuki Y., 2017, Role of demersal zooplankton as a food source for higher trophic levels at Fukido Estuary, Ishigaki Island, Okinawa, Japan, International Journal of Marine Science, 7(17): 161-175 (doi: 10.5376/ijms.2017.07.0017)


Demersal zooplankton (DZ) appear in the water column at night, and are highly abundant in mangrove, seagrass, and coral reef habitats; however, few studies have discussed their role in aquatic food webs, considering different consumers and their preferences on different DZ’ size classes. This study elucidates the role of DZ as a food source for higher trophic levels in an estuarine area, particularly with respect to the food preference and size selection of their consumers. The study was conducted in the mangrove forest of Fukido Estuary and an adjacent reef lagoon (with seagrass-dominated and seagrass-coral mixture areas) on Ishigaki Island, Japan. The abundance of demersal zooplankton was 4.0, 5.4, and 11.3×104 ind.m-2 for seagrass, mangrove, and seagrass-coral mixture habitats, respectively. The lowest DZ biomass was recorded in mangroves and mainly dominated by smaller organisms, because their consumers in this habitat prefer large-sized prey. The δ13C and δ15N signatures showed that, in mangroves, demersal zooplankton constituted a higher proportion of the diet of fishes than in lagoon habitats; however, demersal zooplankton did not have a significant role in the diet of fishes and macroinvertebrates in the lagoon. Consistency among biomass, stomach contents, and the proportions of DZ of all size classes in the diet of mangrove fishes indicated that DZ serve as a major food source. In contrast, fishes in lagoon habitats consumed more crabs, shrimps and mollusks than DZ. In conclusion, our analytical approach allowed us to demonstrate that DZ of different body sizes serve as food sources for different consumers in different habitats of the estuarine ecosystem.

Demersal zooplankton; Biomass; Stable isotope; Mangrove; Seagrass; Seagrass-coral mixture


Mangroves, seagrasses, and coral reefs are important marine coastal ecosystems because they sustain high biodiversity (Zieman et al., 1984; Marguillier et al., 1997) and are highly efficient at transferring organic matter from primary producers to higher trophic levels (Nagelkerken, 2009). These well-structured ecosystems provide stable nursery sites and a wide range of food sources for diverse fishes and invertebrates (Beck et al., 2001; Touchette, 2007; Melo et al., 2010). These habitats accumulate a large quantity of non-living organic matter in their sediments in the form of detritus, leaf litter, and decomposed dead organisms (Kristensen et al., 2008; Bouillon and Connolly, 2009). However, few species of consumers are able to utilize this food source directly. Thus, sediment detritivores and herbivores might be important for connecting these food webs by transferring energy from primary producers to higher trophic levels (Sogard, 1984; Mascart, 2010). Previous studies have reported that demersal zooplankton (DZ) are important for linking small particles (detritus and primary producers attached to sediments) to planktivorous fishes (Morgan, 1990; Boltovskoy, 1999).


DZ reside (or hide) near the substrate during the daytime, emerge at night when they spend a short time in the water column, and return to the substratum before sunrise (Hobson and Chess, 1979; Alldredge and King, 1980; Melo et al., 2010). According to Alldredge and King (1980), the night-time migration of DZ has several advantages, including feeding (on small organisms, such as pico- and nano- size plankton or smaller DZ), reproduction (polychetes spawn at the surface, amphipods mate in the water column), escape from predation by benthic invertebrates, ecdysis, and dispersal to potentially more favorable locations to reduce competition for food and space. Studies have shown that large numbers of DZ emerge from the seagrass, coral reefs, soft bottoms, and kelp beds at night (Youngbluth, 1982; Mascart, 2010; Jayabarathi et al., 2012;). Thus, they might serve as an important food source for planktivores (Melo et al., 2010). However, few studies (Smith et al., 1979; Chew et al., 2012) have investigated how DZ are linked to their consumers in the aquatic food web of coastal ecosystems.


In the food webs of natural systems, it is difficult to determine the proportional contribution of food sources to the diet of consumers on the basis of stomach contents, because the food is rapidly digested in comparison to the slow digestion of non-living organic matter derived from sediments (Fry and Ewel, 2003). As a result, there has been an increasing number of studies using dual stable carbon and nitrogen isotopes to determine the relationship between predators and their food sources (Fry, 2007; Nakamura et al., 2008; Pasquaud et al., 2010; Vinagre et al., 2012; Tue et al., 2013). The δ15N in the tissues of a consumer is typically 2.6‰ to 3.4‰ richer than that in their prey; thus, δ15N studies are often conducted to estimate the trophic position of species in the food web (Deniro and Epstein, 1981; Post, 2002; Fry, 2007). The δ13C of a consumer increases by 0‰ to 1‰ with respect to their food sources (Michener and Lajtha, 2008; Tue et al., 2013). Therefore, the δ13C signature could be used to trace the carbon pathway when the δ13C value of food sources differs across prey items (Bouillon et al., 2008). The stable isotope analysis in R (SIAR) isotopic mixing model (Parnell and Jackson, 2013) is increasingly being applied to estimate the proportions of various food sources ingested by a consumer, on the basis of the isotopic signatures of consumers, food sources, and the trophic enrichment factor (TEF) (Tue et al., 2013). The SIAR model is an open-source package that uses Bayesian inference to address natural variation and the uncertainty of stable isotope data to calculate the probability of food source contributions as percentages of the total diet (Pacella et al., 2013).


In the present study, we hypothesized that DZ contribute in major proportion to the diet of higher trophic levels at Fukido estuarine aquatic food web, and these consumers preferentially feed on DZ of different size classes. We tested this hypothesis by (1) analyzing the abundance and biomass of DZ in a mangrove and an adjacent lagoon (seagrass dominated and seagrass-coral mixture) habitat, to assess the potential amount of DZ that serves as a food source, and (2) determining the proportion of DZ of different size classes in the diets of fishes and macro-invertebrates distributed in mangrove and reef lagoon area, by combining the isotopic mixing model (SIAR) with stomach content analysis. This study is expected to provide new insights on the role and importance of DZ as a food source for consumers at the three sub-environments that compose the Fukido estuary.


1 Materials and Methods

1.1 Study area

The study was carried out in the Fukido Estuary, which is located on the Itona Coast of Ishigaki Island, at the southern tip of Japan (Figure 1A). We focused on the mangrove (MG) habitat at the mouth of Fukido River and the adjacent coral reef lagoon (LG) habitat, which is dominated by shallow seagrass (SG), followed by a zone where seagrass is mixed with coral colonies (SG+CR). The MG habitat extends from the mouth of the Fukido River (mouth is 10-40 m across) and continues 300 m upstream, covering an area of about 18.7 ha (Kurosawa, 2003). Rhizophora stylosa, Bruguiera gymnorrhiza, Kandelia candel, and Lumnitzera racemose dominate the mangrove forest. In the center of the river mouth, the water depth ranges from 0.5 to 1 m at low tide and 1 to 2 m at high tide, where mangrove prop roots are alternately inundated and exposed, during the tidal cycle (Nakamura et al., 2008; Shibuno et al., 2008). The seagrass bed (water depth range of 0.5-1 m at low tide and 2-3 m at high tide) extends for about 2.5 km along the coast at a distance of 30 to 120 m offshore, and is dominated by Thalassia hemprichii (Shibuno et al., 2008). Toward the middle of the lagoon, seagrass mixes with some coral colonies. Branching corals (mainly Montipora spp.) and massive corals (especially Porites spp.) dominate in this area of coexistence. During the flood tide, seawater passes over a large sill across the mouth of the river (Figure 1C) and flows backward, inundating the mangrove forest. During the ebb tide, the water flows out through a small canal across the sand sill to the lagoon area. This sill completely separates mangrove water from lagoon water (Nihei et al., 2002; Kurosawa, 2003).



Figure 1 A: Map of Fukido Estuary, Ishigaki, Okinawa, Japan; ▲ indicates the position of trap set-up and sampling areas; MG: Mangrove area; SG: Seagrass area and SG+CR: Seagrass mixed with Coral area; B: Emergence trap with a mesh size of 73 mm; C: Vertical section of the sampling area (LG: Lagoon)


1.2 Sample collection

Sampling was carried out at MG, SG, and SG+CR in March 2015 and 2016 (Figure 1A). Two bait traps (10 m long and 6 mm mesh size) were set overnight in each area to collect fishes and macro-invertebrates. The muscle tissues of fishes and macro-invertebrates were used for stable isotope analysis, because the constant isotopic value of this tissue reflects the isotopic value of food sources utilized over long periods (i.e., several weeks to months) (Herzka, 2005).


The leaves of mangrove species (Rhizophora stylosa) and seagrass species (Thalassia hemprichii and Halodule pinifolia) were collected by hand in the mangrove and seagrass areas, respectively. Mangrove and seagrass leaves were washed with MQ pure water (Arium® 611VF, Sartorius Stedim Biotech GmbH, Germany) to remove all detritus before it was stored at -20°C until further treatment. Phytoplankton samples were collected using a plankton net. In both habitats, 100 L of seawater was pre-filtered using a mesh with a pore size of 73 mm to remove large material (e.g., detritus, zooplankton). Phytoplankton was captured using a mesh size of 10 mm. Retained phytoplankton were filtered onto pre-combusted Whatman GF/F filters (~0.7 mm) and were stored at -20°C. Aliquots of the surface sediment (upper 2 cm) were sampled to study primary microbial producers. These aliquots were homogenized and stored in Corning tubes (50 mL) at -20°C.


DZ were collected with a modified “emergence trap” of conical shape, according to Hobson and Chess (1979), using 2 chambered traps with a mesh size of 73 µm (Figure 1B). Three demersal traps were set-up at MG, SG, and SG+CR. The mouth of each trap was fixed at 5 cm under the sediment surface using soil anchors, and was set up from 18:00 to 07:00 of the next day. DZ samples were separated into fractions using sieves; these fractions were: 73 µm (73 to 100 µm), 100 µm (100 to 250 µm), 250 µm (250 to 500 µm), 500 µm (500 to 1000 µm), 1000 µm (1000 to 2000 µm), and greater than 2000 µm (>2000 µm). Then the fractions were divided into 2 sub-samples: one for identification, for which zooplankton was fixed in 5% formalin, and one for stable isotope analysis (SIA). The SIA samples of demersal zooplankton were examined under the stereomicroscope (SMZ 1000, Nikon Inc., Tokyo, Japan) to remove detritus to avoid contaminating the isotopic signal. The SIA samples of demersal zooplankton were then stored at -20°C until isotopic analysis.


1.3 Determining the abundance and biomass of DZ

DZ was identified and counted under a stereomicroscope (SMZ 1000, Nikon Inc.). The abundance of DZ taxa was calculated as the number of individual m-2 (ind.m-2) on the bottom surface area, based on the mouth area of the “emergence trap” (Figure 1B). The carbon biomass of DZ was calculated as the carbon content in µg C ind-1, based on the taxonomic level and the average size class, using the regression equation given by Heidelberg et al. (2010): LN (Copepod biomass) = 1.82 × log (L) + 1.28 (r2 = 0.893, df = 16, F = 125; sig. = 1.12 × 10-8) and LN (Other taxa biomass) = 1.46 × LN (L) + 1.03 (r2 = 0.733, df = 16, F = 80.7; sig. = 3.47 × 10-7), where LN is the natural logarithm and L is the average size (length) in mm.


1.4 Analysis of fish stomach content

The stomach and gut were dissected from the fish body and preserved with 90% ethanol. The stomach content was observed under a stereomicroscope (SMZ 1000, Nikon Inc.), and the percentage of items present was estimated. The food sources were identified to the lowest possible taxon.


1.5 Sample treatment

Sediment containing bacteria, small primary producers, and fine detritus was dried at 60°C in an oven to a constant weight (around 20 h), and was then passed through a sieve with a pore size of 63 mm to separate out large particles (coarse gravel, mangrove detritus, seagrass roots, and mollusk shells). Sediment powder was homogenized for sediment SIA. The litter that remained on the sieve (< 200 mm) that was derived from mangrove and seagrass was ground to a fine powder for detritus stable isotope analysis. The other SIA samples were dried at 60°C until a constant weight was reached. Then, the samples were ground to a fine powder.


The homogeneous powder of the SIA samples was divided into 2 fractions for δ15N and δ13C analysis. The samples for δ15N were stored in a dry box until analysis without acid treatment to prevent acidification affecting the δ15N values (Bunn et al., 1995; Mateo et al., 2008). The samples for δ13C analysis were further treated to remove the lipid content and carbonates. In brief, the lipid content in animal tissue can alter the results and conclusions of δ13C analysis in the aquatic food web and migration studies (Bunn et al., 1995; Focken and Becker, 1998). Thus, in the present study, fishes and macroinvertebrate samples were treated to remove lipids following a method modified from Logan et al. (2008). Specifically, dried powder samples were placed in centrifuge tubes to which a solvent with a 2:1 ratio of chloroform:methanol was added, with a volume 3 to 5 times larger than the sample size. Samples were mixed for 30 s in an MS1 Minishaker (IKA® Works (Asia) Sdn. Bhd., Malaysia) at 1000 rpm. The samples were then left undisturbed for about 20 min, after which they were centrifuged at 2500 × g for 10 min. The supernatant containing the solvent and lipids was discarded. This process was repeated until there was an entirely clear supernatant. After removing the lipids, the animal tissues were subjected to an acidification procedure to remove carbonates. The samples (animal tissues, sediment, and seagrass leaves) were acidified by dropping a solution of 1 N HCl onto the sample until bubbling ceased (Jacob et al., 2005). Then, the samples were washed 3 times with Milli-Q water before being dried at 60°C to a constant weight and ground to a fine powder. DZ samples and phytoplankton trapped on GF/F were fumed with concentrated 12 N HCl in a glass desiccator for 12 h to remove carbonates, and were then dried at 60°C to a constant weight and ground to a fine powder. All powder samples were stored in Eppendorf tubes inside a dry box until analysis.


1.6 Stable carbon and nitrogen isotope analysis

Stable carbon and nitrogen isotopes were analyzed at the Laboratory of Aquatic Animal Ecology, School of Marine Biosciences, Kitasato University, Japan. The samples were dried in an electric oven at 60°C for 6 h before analysis. Subsamples of 0.5 ± 0.07 mg (Mean ± SD) dry weight for fishes and macroinvertebrates tissues and 2.0 ± 0.08 mg (Mean ± SD) dry weight for DZ were placed in ultra-pure tin capsules, and the samples were burned in an elemental analyzer (Flash EA, Thermo Fisher Scientific, Waltham, MA, USA). Combustion gasses continuously moved through a flow controller (ConFlo, Thermo Fisher), and then the stable carbon and nitrogen isotope compositions were detected with a mass spectrometer (DeltaplusXP, Thermo Fisher). L-alanine was used as the working standard. Repeated measurements of the standard showed a standard deviation of 0.2‰ or less. Stable isotope ratios were expressed in δ notation (part per thousand, ‰) as deviations from international standards according to the following equation:


δX = (Rsample/Rstandard – 1) × 1000


Where X represents 13C or 15N, and R represents isotope ratios 13C/12C or 15N/14N, respectively. Rsample and Rstandard are the isotope ratio of the sample and working standard, respectively.


1.7 Estimation of proportional contribution from food sources

The SIAR package (Parnell and Jackson, 2013) of R software (R Core Team, 2015) was used to calculate the proportion of total diet that was contributed by food sources, based on the stable isotope values of consumers, the mean and standard deviation (SD) stable isotope values of food sources, and the trophic enrichment factor (TEF) of food sources. To compare the percentage of DZ with other food sources at each of the selected habitats, we estimated the contribution of food sources to the diets of consumers (fishes, macroinvertebrates) in each habitat using the mean of the TEF (± SD) for δ13C and δ15N as 0.4 ± 1.3‰ and 3.4 ± 1.0‰, respectively (Post, 2002). On the basis of the results of the stomach contents analysis, we compared DZ against other food sources (including crabs, shrimps, mollusks and, detritus) in the diet of fishes. In the diet of macro-invertebrates, we compared DZ against the plant (mangrove or seagrass) leaves, phytoplankton, detritus, and sediment.


1.8 Statistical analysis

The Shannon diversity index (Hʹ) was calculated to estimate the diversity of the DZ community. One-way ANOVA was performed to test the differences (p < 0.05) in the isotopic values of DZ and their proportion in the diets of consumers.


2 Results

2.1 Composition of DZ communities

In the present study, 18 DZ taxa were identified (Table 1). The species groups that had high-frequency distributions and higher abundance in all 3 habitats were Harpacticoida (copepodite), Foraminifera, and Gammaridea (Table 1). In the MG habitat, Harpacticoida (copepodite) contributed 43.2%, followed by Nematoda (24.3%) and the nauplii of Copepoda (10.8%). In the SG habitat, Foraminifera contributed 27.8%, followed by Isopoda (22.2%). In the SG+CR habitat, Oithona rigida had the highest abundance (25.7%), followed by the nauplii of Copepoda (22.9%) and Harpacticoida (copepodite) (12.9%).



Table 1 Composition, size range, and relative abundance (%) of demersal zooplankton captured by emergence traps


The diversity index (Hʹ) increased from MG (1.6) towards SG+CR (2.2) habitat (Figure 2A). DZ abundance was highest in SG+CR (11.3 × 104 ind.m-2), followed by MG (5.4 × 104 ind.m-2) and SG (4.0 × 104 ind.m-2) (Figure 2A). When analyzing the biomass of the different size classes, we observed that the larger size classes (i.e., 500 to 1000 µm, 1000 to 2000 µm, and >2000 mm) contributed more to the total biomass of SG and SG+CR compared to MG (Figure 2B). The biomass contributions of the smaller size classes (73 mm, 100 µm, 250 µm) were similar in both MG and SG habitats. Small organisms mainly dominated the total DZ biomass in the MG habitat. Moreover, the total biomass in MG (205.2 × 103 µg C m-2) was lower than the total biomass in SG (341.1 × 103 µg C m-2) and SG+CR (709.0 × 103 µg C m-2) (Figure 2B). Thus, the MG habitat contained smaller organisms, with the lower abundance dominating the total biomass. This abundance was lower than the total biomass of DZ in SG and SG+CR.



Figure 2 A: Abundance and Shannon index: ind. m-2 (mean ± SD), Shannon diversity index (Hʹ) and B: Biomass within size classes of demersal zooplankton at Fukido Estuary


2.2 Stomach contents of fishes

Table 2 shows the stomach contents of 11 fish species collected in Fukido Estuary. The preferred foods of fishes in MG were zooplankton, which are components of DZ (Table 1). Fishes from MG primarily consumed copepods (5-15%) and polychetes (5-25%), followed by amphipods (3-10%), nematodes (5-10%), and foraminifers (2-5%). Some fishes, such as Y. cringer (2%), C. punctata (5%), F. amboinensis (7%), and Lutjanus sp. (20%) consumed crabs. Shrimp and mollusks were consumed by larger fishes, such as Lutjanus sp. (10%) and A. semipunctata (10%), respectively (Table 2). However, the main stomach content of some fish specimens in MG was detritus (G. oyena [80%] and A. semipunctata [50%]) and fine soil and sand grains (F. amboinensis [40%] and Z. dunckeri [30%]) (Table 2). Fish specimens collected in the LG habitat mainly consumed crabs (10-15%), mollusks (10-30%), and shrimp (10%). Moreover, some fishes consumed DZ species, such as amphipods (20-30%), copepods (10%), and polychetes (5%), in the lagoon habitat (Table 2).


Table 2 Fish in Mangrove and Lagoon habitats and the average percentage of the prey items recorded in their stomach contents in Fukido Estuary

Note: Cr: crabs (crab + hermit crab), Sh: shrimps, Mo: Mollusks, Demersal zooplankton (Ne: nematodes, Co: copepods, Am: amphipods, Iso: isopods, Po: polychetes, Fo: Foraminifers), Al: macro algae, Sg: seagrass, Se: sediment, De: detritus, Other: small material and unidentified foods; TL = total length; n = number of samples


2.3 Isotopic signature of consumers, DZ, and other food sources

Figure 3 shows the stable carbon and nitrogen isotope signatures of DZ, other food sources (mangrove leave, seagrass leave, detritus, sediment, and phytoplankton), and their consumers (fishes, crabs, shrimps and mollusks) in the aquatic food web of Fukido Estuary. The δ13C values of DZ ranged from -24.9 to -20.4‰ and -20.5 to -15.4‰ in the MG and LG areas, respectively. The δ15N signatures of DZ in both habitats were not significantly different (ANOVA, p = 0.479), ranging from 2.7 to 4.6‰ (Figure 3).


The δ13C and δ15N values of other food sources (mangrove and seagrass leaves, phytoplankton, detritus, and sediment) ranged from -29.4 to -25.9‰ and 0.6 to 2.1‰, respectively, in MG; and from -21.3 to -10.3‰ (δ13C) and 0.7 to 1.8‰ (δ15N) in the LG habitat. The δ13C and δ15N values of consumers ranged from -26.7 to -18.8‰ and 4.3 to 9.3‰ in MG, respectively. In comparison, these signatures ranged from -14.2 to -11.0‰ (δ13C) and from 4.2 to 9.7‰ (δ15N) in the lagoon habitat (Figure 3).



Figure 3 Carbon and nitrogen isotopic signatures (mean ± SD) of demersal zooplankton, their consumers, and other food sources in Fukido Estuary

Note: The symbols indicate demersal zooplankton (Δ), fishes (◊), crabs (□), mollusks (○), and shrimps (x). Solid black filled symbols denote organisms collected in the mangrove, and open symbols denote samples collected from the lagoon (SG and SG+CR). Dotted lines indicate other food sources derive from mangrove (MG) and lagoon (LG) habitats; Label abbreviations are shown in Table 3 and Table 4




Table 3 Proportion of demersal zooplankton and other food sources in the diet of fishes in Fukido Estuary

Note: The mean and the 90% credibility intervals (5% and 95%) of the proportions are reported for each potential food source in the fish diet. DZ.73, DZ.100, DZ.250, DZ.500, DZ.1000, and DZ.2000 denote the demersal zooplankton size classes of 73 to 100 µm, 100 to 250 µm, 250 to 500 µm, 500 to 1000 µm, 1000 to 2000 µm, and larger than 2000 (µm), respectively




Table 4 Proportion of demersal zooplankton and other food sources in the diet of macroinvertebrates in Fukido Estuary

Note: The mean and the 90% credibility intervals (5% and 95%) of the proportions are reported for each potential food source in the macroinvertebrate diet. DZ.73, DZ.100, DZ.250, DZ.500, DZ.1000, and DZ.2000 denote demersal zooplankton size classes of 73 to 100 µm, 100 to 250 µm, 250 to 500 µm, 500 to 1000 µm, 1000 to 2000 µm, and larger than 2000 (µm), respectively. Phyto- is phytoplankton, Plant is mangrove leaves and seagrass leaves in mangrove and lagoon habitats, respectively


2.4 Proportional distribution of DZ in the diets of higher trophic levels

The contributions of the potential food sources of the fishes and macro-invertebrates in Fukido Estuary are presented in Table 3 and Table 4, respectively. Table 3 shows that DZ of larger size classes (500 to 2000 mm) contributed more to the diet of MG fishes than the DZ of smaller size classes (73 to 250 mm). In the diet of some mangrove fish species, the proportional contribution of DZ from the larger size classes (500 to 2000 mm) was higher than that of other food sources (e.g., crabs, shrimp, mollusks, and detritus). A. semipunctata consumed large quantities of DZ large than 2000 mm (15.0%), followed by 500–1000 mm DZ (13.4%) and 1000-2000 mm DZ (12.9%). DZ contributed 11.1-12.5% to the diet of Y. criniger. DZ large than 2000 mm contributed the highest proportion (12.9%) to the diet of Z. dunckeri, followed by 1000-2000 mm DZ (12.6%) and 500-1000 mm DZ (12.1%). Other food sources contributed 4.3-11.7%, 7.1-10.5%, and 7.3-9.7% to the diet of A. semipunctata, Y. criniger, and Z. dunckeri, respectively. In comparison, some mangrove fish species consumed more crabs and shrimps than DZ. For instance, F. amboinensis consumed the highest proportion of crabs (19.0%), followed by shrimps (15.8%). The diet of C. punctate contained 13.1% crabs and 11.7% shrimps. DZ contributed just 6.2-7.8% (73-250 mm size classes) and 8.7-13.6% (500-2000 mm) to the diet of F. amboinensis, and 8.8-9.6% (73-250 mm) and 10.1-11.6% (500-2000 mm) to the diet of C. punctata.


Lutjanus sp. and G. oyena consumed similar quantities of DZ (500-2000 mm) and other crustaceans (such as crabs and shrimps) in MG habitat; however, Lutjanus sp. collected in the LG habitat consumed more crabs (12.2%) and shrimps (11.2%) than DZ (9.8-10.1%). Other lagoon fishes also consumed more on crabs, shrimps, and mollusks than DZ (Table 3).


The results of the mixing model of the macro-invertebrates diet items and their proportions in Fukido Estuary are presented in Table 4. Mangrove crabs (Scylla serrata and Charybdis sp.) consumed more DZ of bigger size classes (500 to 2000 mm) than smaller size classes (73-250 mm) or other food sources (i.e., those derived from mangrove leaves, detritus, sediment, and phytoplankton). In comparison, some macro-invertebrates (such as E. japonica and C. septemspinosa) consumed more DZ of smaller size classes (73-250 mm) than larger size classes (500-2000 mm). Almost all macro-invertebrates (except Charybdis sp. and S. serrata) from both habitats preferentially consumed food sources derived from detritus, sediment, plants, and phytoplankton compared to DZ.


3 Discussion

3.1 Role of DZ as a potential food source in an estuarine food web

Mangroves, seagrasses, and coral reefs support and provide shelter for a large number and high diversity of fish and invertebrates (Zieman et al., 1984; Larkum et al., 2007). The average size ratio of predator to prey is usually around 10 to 1, while the abundance ratio is typically the inverse (Litchman et al., 2013; Chen and Terry, 2014). Therefore, DZ must contribute substantially to the system, as a large reserve of highly abundant food source with a wide range of body dimensions. Previous studies reported that DZ are highly abundant in shallow habitats (Melo et al., 2010). DZ usually reside in the top 3 cm of the sediment, emerging in large numbers at night and occupying the water column up to 30 cm from the bottom (Alldredge and King, 1985). They only remain in the water column for a short time to avoid predators that use vision to locate their prey (Alldredge and King, 1985). In the present study, DZ abundance ranged from 4.0 to 11.3 × 104 ind.m-2 (Figure 2A), with a wide range of body sizes being detected (75 to 9100 µm) (Table 1). At Fukido Estuary, the abundance of DZ was higher than that previously reported in other geographical areas. For instance, Melo et al. (2010) reported comparatively lower DZ abundance (5 × 103 ind.m-2) in a seagrass area in the southwestern Atlantic Ocean. In comparison, the abundance of DZ in Onslow Bay (North Carolina, USA) ranged from 1 to 6 × 104 ind.m-2 depending on substrate structure and season (Cahoon and Tronzo, 1992).


The biomass of DZ in the 1000-2000 µm and > 2000 µm size classes were lower than those smaller size classes in MG compared to that in the other habitats (Figure 2B). Compared to that in the other habitats in our study, the abundance of DZ in MG was intermediate, with smaller biomass. Sultana et al. (2016) reported that the sediment in mangrove habitat supports high primary production. Thus, DZ might be present in higher abundance and biomass than that detected in our study. However, our results showed that smaller DZ contributed the most to DZ biomass, indicating that higher trophic level organisms preferentially consume larger DZ (Figure 2). Therefore, DZ with lower biomass and of smaller size might remain in the mangrove habitat. This suggestion is supported by the result of the mixing model used to estimate the proportion of DZ in the diet of fishes (Table 3). This model showed that the proportional contribution of larger DZ (500-2000 mm) were higher than that of smaller DZ (73-250 mm) in the diet of almost all mangrove fishes. Thus, consumers in the mangrove area might actively feed on more DZ than previously thought (Nakamura et al., 2008; Tue et al., 2013). This hypothesis is consistent with the stomach contents of fishes, which showed that the mangrove fishes primarily fed on DZ compared to other food sources (Table 2).


3.2 Proportional contribution of DZ in the diet of consumers

Estimation of the proportional contributions of prey in the diet of consumers in coastal ecosystems is traditionally performed by analyzing stomach contents. This method is convenient because it can be carried out rapidly and economically, providing a direct estimation of prey contents (Hyslop, 1980; Pasquaud et al., 2010; Winemiller et al., 2011). However, stomach content analysis has some limitations, because living organisms digest food more rapidly than non-living organic matter (Fry and Ewel, 2003). The SIAR mixing model is based on the isotopic signatures of prey and consumers, and has been increasingly used to determine the proportional contributions of food sources (Parnell et al., 2010). In this study, we combined both methods (stomach content and mixing model) to clarify and highlight the contributions of DZ to the diet of fishes and macroinvertebrates at Fukido Estuary.


The mixing model showed that DZ contributed more to the diet of mangrove fishes than other food source in the MG habitat, particularly for A. semipunctata, Y. criniger, and Z. dunckeri (Table 3). In particular, these fish species consumed larger DZ (of 500 to 2000 mm), which were dominated by nematodes, polychetes (larvae), copepods, amphipods, and gammarids (Table 1). The results of the stomach content analysis supported this observation (Table 2). Our results were also consistent with those of previous reports (Masuda et al., 1984; Rainboth, 1996; Myers, 1999). In comparison, crabs and shrimp contributed to the diet of F. amboinensis and C. punctata more than DZ. Other studies also reported that F. amboinensis primarily consumes small crustaceans (Masuda et al., 1984), whereas C. punctata preferentially feeds on small benthic invertebrates and small crabs (Knapp, 1999). However, our stomach content analyses of these fishes showed that they preferentially fed on nematodes and copepods compared to crabs and shrimps (Table 2). This discrepancy might be explained by the fact that stomach contents only reflect feeding events, rather than assimilated material; consequently, this type of analysis is biased by the differences in digestibility of prey items (Polunin and Pinnegar, 2002). Thus, the proportions of food sources based on isotopic analysis probably provides a more accurate picture of feeding behavior than stomach contents. Our results showed that mangrove fishes predominantly fed on DZ compared to other food sources. In comparison, lagoon fishes consumed more crabs, shrimps, and mollusks than DZ. These differences were supported by both the results of the mixing model (Table 3) and the stomach contents analysis (Table 2). Lagoon fishes of large body size might preferentially feed on larger food sources. This suggestion was supported by the results of the feeding preferences of Lutjanus sp., which is a migratory fish that frequents Fukido Estuary (Nakamura et al., 2008). Juvenile stage Lutjanus sp. are relatively small (around 30-125 cm) (Nakamura et al., 2008; Shibuno et al., 2008), and they inhabit MG as a nursery. Juvenile Lutjanus sp. consumed similar proportions of DZ (500-2000 mm) as crabs and shrimps in MG (Table 3), perhaps because the Lutjanus sp. might prefer DZ than crustaceans that have hard exoskeletons. As adults, when their body size becomes greater than 150 cm, Lutjanus sp. migrate to the lagoon area (Nakamura et al., 2008), where they switch their feeding preference to crustaceans (crabs and shrimps) during ontogenetic migration (Table 2; Table 3). Thus, DZ might be an important food source for fishes in mangrove habitats compared to other studied habitats.


Benthic macroinvertebrates are distributed in all coastal ecosystems (mangrove, seagrass and coral reef, etc.), and inhabit areas on or near the seabed (Attrill, 1998; Castro et al., 2008; Barnes, 2013; Kumar and Khan, 2013). This group exhibits diverse ecological niches and invests in a variety of feeding behaviors. For instance, there are deposit feeders (mainly polychetes and some mollusks), detritivores (some echinoderms and crustaceans), predators (echinoderms and crustaceans), filter feeders (mainly bivalves and crustaceans), among others. Our dataset showed that DZ contributed more than other food sources to the diet of 2 crab species (Scylla serrata and Charybdis sp.) (Table 4). Other studies have also reported that these 2 crab species preferentially feed on fishes, crustaceans, mollusks, and polychetes in mangrove habitats (Sara et al., 2007; Wikipedia, n.d.). The stable carbon and nitrogen isotope signature of S. serrata are comparable to that of some mangrove fishes (Z. dunckeri, A. semipunctata, F. amboinensis) (Figure 3); thus, these crabs probably feed on food sources similar to fishes, preferentially selecting large-sized DZ. This suggestion was supported by the results of the mixing model on the diet of S. serrata, which showed that they feed on larger rather than smaller DZ (Table 4). In contrast, some species (such as E. japonicas and C. septemspinosa) primarily consumed food sources that were derived from detritus, sediment, and plant debris rather than DZ (Table 4). This result supports that obtained by previous report (Kolpakov et al., 2012). Other macroinvertebrates (except Scylla serrata and Charybdis sp.) appeared to consume similar quantities of small (73-250 mm) and large DZ in the lagoon habitat, but preferentially fed on smaller DZ in mangrove habitat (Table 4).


4 Conclusions

This study demonstrated that DZ are an important food source in Fukido Estuary. The mangrove habitat supported the lowest DZ biomass, and was mostly made up of small-sized DZ. Thus, higher trophic level organisms might consume large-sized DZ, resulting in the smaller sizes remaining (unconsumed) in the mangrove habitat. This suggestion supports the proportions of DZ size classes detected in the stomach contents of mangrove fishes. Large percentages of DZ were detected in the stomachs of mangrove fishes, confirming their importance as a food source. In contrast, DZ did not have a significant role in the diet of fishes in lagoon habitats compared to other food sources. The combined results of abundance and biomass with the proportions of DZ in the diet of consumers highlight the important role of DZ in the diet of active feeders in mangrove habitats compared to that in other habitats. To our knowledge, this study is the first attempt to elucidate the role of DZ within the food web of an estuary, using the stable isotope mixing model of size class and biomass combined with direct observations of stomach contents. In conclusion, we showed that the suggested approach (combining stable isotope mixed models with stomach content observations) was reliable, demonstrating that DZ of different body sizes serve as food sources for different consumers in different habitats.


Authors’ contributions

HMV, BEC, LS, and YS designed the study, conducted the experiments, and collected the samples. HMV, BEC, and KT identified demersal zooplankton and stomach contents. HMV and KH completed the stable isotope analysis. All authors read and approved the final manuscript.



We thank Mr. S. Tamada of the Laboratory of Aquatic Animal Ecology, School of Marine Biosciences, Kitasato University for the supporting the stable isotope analysis. We also thank Mr. S. Uehara (Growing Coral Co.) for providing support during the fieldwork, and we thank the International Coral Reef Research & Monitoring Center, Ministry of Environment, Ishigaki, Japan for providing laboratory facilities. The Environmental Leaders Program of Shizuoka University Corporation (ELSU) and the Global Coral Reef Conservation Project (GCRC) of Mitsubishi Corporation supported this study. This study was conducted under the umbrella of Core-to-Core Program and Asian CORE Program of the Japan Society for the Promotion of Science.




Alldredge A.L., and King J.M., 1980, Effects of moonlight on the vertical migration patterns of demersal zooplankton, Journal of Experimental Marine Biology and Ecology, 44: 133-156


Alldredge A.L., and King J.M., 1985, The distance demersal zooplankton migrate above the benthos: implications for predation, Marine Biology, 84: 253-260


Attrill M., 1998, The benthic macroinvertebrate communities of the Thames Estuary, In: Attrill, M. J. (Ed.) A Rehabilitated Estuarine Ecosystem: The environment and ecology of the Thames Estuary, Springer US, Boston, MA, pp.85-113


Barnes R.S., 2013, Distribution patterns of macrobenthic biodiversity in the intertidal seagrass beds of an estuarine system, and their conservation significance, Biodiversity & Conservation, 22: 357-372


Beck M.W., Heck K.L.J., Able K.W., Childers D.L., Eggleston D.B., Gillanders B.M., Halpern B., Hays C.G., Hoshino K., Minello T.J., Orth R.J., Sheridan P.F., and Weingstein M.P., 2001, The identification, conservation, and management of estuarine and marine nurseries for fish and invertebrates, Bioscience, 51: 633-641[0633:TICAMO]2.0.CO;2


Boltovskoy D., 1999, South Atlantic Zooplankton, Backhuys Publisher, Leiden, The Netherland, pp.1722


Bouillon S., Borges A., Casta, Eda-Moya E., Diele K., Dittmar T., Duke N., Kristensen E., Lee S., Marchand C., Middelburg J., Rivera-Monroy V., Thomas, and Twilley R., 2008, Mangrove production and carbon sinks: A revision of global budget estimates, Global Biogeochemical Cycles, 22: 1-12


Bouillon S., and Connolly R., 2009, Carbon exchange among tropical coastal ecosystems, In: Nagelkerken, I. (Ed.) Ecological connectivity among tropical coastal ecosystems, Springer, The Netherlands, pp.45-70


Bunn S.E., Loneragan N.R., and Kempster M.A., 1995, Effects of acid washing on stable isotope ratios of C and N in penaeid shrimp and seagrass: implications for food-web studies using multiple stable isotopes, Limnology and Oceanography, 40: 622-625


Cahoon L.B., and Tronzo C.R., 1992, Quantitative estimates of demersal zooplankton abundance in Onslow Bay, North Carolina, USA, Marine Ecology Progress Series, 87: 197-200


Castro P., Huber M.E., Ober W.C., and Garrison C.W, 2008, Marine Biology, McGraw-Hill, pp.459


Chen J., and Terry W., 2014, The effect of interference competition in Asplanchna brightwelli on its predation capacity, Journal of Plankton Research, 36: 1391-1395


Chew L.L., Chong V.C., Tanaka K., and Sasekumar A., 2012, Phytoplankton fuel the energy flow from zooplankton to small nekton in turbid mangrove waters, Marine Ecology Progress Series, 469: 7-24


Deniro M.J., and Epstein S., 1981, Influence of diet on the distribution of nitrogen isotopes in animals, Geochimica et Cosmochimica Acta, 45: 341-351


Focken U., and Becker K., 1998, Metabolic fractionation of stable carbon isotopes: implications of different proximate compositions for studies of the aquatic food webs using δ13C data, Oecologia, 115: 337-343



Fry B., 2007, Stable isotope ecology, Springer, New York, USA, pp.302


Fry B., and Ewel K.C., 2003, Using stable isotopes in mangrove fisheries research — A review and outlook, Isotopes in Environmental and Health Studies, 39: 191-196



Heidelberg, K.B., O’Neil, K.L., Bythell, J.C., Sebens, K.P., 2010, Vertical distribution and diel patterns of zooplankton abundance and biomass at Conch Reef, Florida Keys (USA), Journal of Plankton Research, 32: 75–91

PMid:20046854 PMCid:PMC2787388


Herzka S.Z., 2005, Assessing connectivity of estuarine fishes based on stable isotope ratio analysis, Estuarine, Coastal and Shelf Science, 64: 58-69


Hobson E.S., and Chess J.R., 1979, Zooplankters that emerge from the lagoon floor at night at Kure and Midway Atolls, Hawaii, Fishery Bulletin, 77: 275-280


Hyslop E.J., 1980, Stomach contents analysis - a review of methods and their application, Journal of Fish Biology, 1741: 1-429


Jacob U., Mintenbeck K., Brey T., Knust R., and Beyer K., 2005, Stable isotope food web studies: A case for standardized sample treatment, Marine Ecology Progress Series, 287: 251-253


Jayabarathi R., Padmavati G., and Anandavelu I., 2012, Abundance and species composition of Harpacticoid copepods from a sea grass patch of South Andaman, India, Current Research Journal of Biological Sciences, 4: 717-724


Knapp L.W., 1999, Platycephalidae. Flatheads, In: Carpenter K.E., and Niem V.H. (Eds.) FAO species identification guide for fishery purposes. The living marine resources of the Western Central Pacific, FAO, Rome, pp.2385-2421


Kolpakov N.V., Semenkova, E.G., and Shuntov V.P., 2012, Japanese mitten crab of Primorye, TINRO-Centre, Russia, Vladivostok, pp.160


Kristensen E., Bouillon S., Dittmar T., and Marchand C., 2008, Organic carbon dynamics in mangrove ecosystems: A review, Aquatic Botany, 89: 201-219


Kumar P.S., and Khan A.B., 2013, The distribution and diversity of benthic macroinvertebrate fauna in Pondicherry mangroves, India, Aquatic Biosystems, 9: 1-18

PMid:23937801 PMCid:PMC3751066


Kurosawa K., 2003, Analysis of the nitrogen cycling in Fukido mangrove estuary, Dissertation for Ph.D., Graduate School of Science and Engineering, Shizuoka University, Japan, Supervisor: Suzuki Y., pp.147


Larkum A., Orth R.J., and Duarte C., 2007, Seagrasses: Biology, ecology and conservation, Springer, Dordrecht, The Netherlands, pp.707


Litchman E., Ohman M.D., and Kiørboe T., 2013, Trait-based approaches to zooplankton communities, Journal of Plankton Research, 35: 473-484


Logan J.M., Jardine T.D., Miller T.J., Bunn S.E., Cunjak R.A., and Lutcavage M.E., 2008, Lipid corrections in carbon and nitrogen stable isotope analyses: comparison of chemical extraction and modeling methods, Journal of Animal Ecology, 77: 838-846



Marguillier S., Velde v.d G., Dehairs F., Hemminga M.A., and Rajagopal S., 1997, Trophic relationships in an interlinked mangrove-seagrass ecosystem as traced by δ13C and δ15N, Marine Ecology Progress Series, 151: 115-121


Mascart T., 2010, The role of meiofauna in the energy transfer in a Mediterranean seagrass bed (Calvi, Corsica). Thesis for M.S., Department of Marine Biology, Marine and Lacustrine Sciences, Ghent University, Supervisor: Marleen De Troch, pp.26


Masuda H., K. Amaoka C., Araga T., Uyeno, and Yoshino T., 1984, The fishes of the Japanese Archipelago, Tokai University Press, Tokyo, Japan, pp.437


Mateo M.A., Serrano O., Serrano L., and Michener R.H., 2008, Effects of sample preparation on stable isotope ratios of carbon and nitrogen in marine invertebrates: implications for food web studies using stable isotopes, Oecologia, 157: 105-115



Melo P.a.M.C., Silva T.A., Neumann-Leitão S., Schwamborn R., Gusmão L.M.O., and Porto Neto F., 2010, Demersal zooplankton communities from tropical habitats in the southwestern Atlantic, Marine Biology Research, 6: 530-541


Michener R., and Lajtha K., 2008, Stable isotopes in ecology and environmental science, Backwell Publishing, USA, pp.563


Morgan S.G., 1990, Impact of planktivorous fishes on dispersal, hatching, and morphology of estuarine crab larvae, Ecology, 71: 1639-1652


Myers R.F., 1999, Micronesian reef fishes: A comprehensive guide to the coral reef fishes of Micronesia, Coral Graphics, Barrigada, Territory of Guam, USA, pp.330


Nagelkerken I., 2009, Ecological connectivity among tropical coastal ecosystems, Springer, pp.615


Nakamura Y., Horinouchi M., Shibuno T., Tanaka Y., Miyajima T., Koike I., Kurokura H., and Sano M., 2008, Evidence of ontogenetic migration from mangroves to coral reefs by black-tail snapper Lutjanus fulvus: stable isotope approach, Marine Ecology Progress Series, 355: 257-266


Nihei Y., Nadaoka K., Aoki Y., Wakaki K., Yai H., and Furukawa K., 2002, An intensive field survey of physical environments in a mangrove forest, 12th International Society of Offshore and Polar Engineers, ISOPE, Kitakyushu, Japan, pp.357-361


Pacella S.R., Lebreton B., Richard P., Phillips D., Dewitt T.H., and Niquil N., 2013, Incorporation of diet information derived from Bayesian stable isotope mixing models into mass-balanced marine ecosystem models: A case study from the Marennes-Oléron Estuary, France, Ecological Modelling, 267: 127-137


Parnell A., and Jackson A., 2013, SIAR: Stable Isotope Analysis in R


Parnell A.C., Inger R., Bearhop S., and Jackson A.L., 2010, Source partitioning using stable isotopes: Coping with too much variation, PLoS ONE, 5: 1-5

PMid:20300637 PMCid:PMC2837382


Pasquaud S., Pillet M., David V., Sautour B., and Elie P., 2010, Determination of fish trophic levels in an estuarine system, Estuarine, Coastal and Shelf Science, 86: 237-246


Polunin N.V.C., and Pinnegar J.K., 2002, Trophic ecology and the structure of marine food webs, In Hart, J.B.P., and Reynolds, D.J. (Eds.) Handbook of fish biology and fisheries, Blackwell Publishing Ltd, Oxford, UK, pp.301-320


Post D.M., 2002, Using stable isotopes to estimate trophic position: models, methods, and assumptions, Ecology, 83: 703–718[0703:USITET]2.0.CO;2


R Core Team, 2015, R: A Language and Environment for Statistical Computing. Vienna, Australia, R Foundation for Statistical Computing. URL


Rainboth W.J., 1996, Fishes of the Cambodian Mekong. FAO species identification field guide for fishery purposes, FAO, Rome, pp.265


Sara L., Ingles J.A., Baldevarona R.B., Aguilar R.O., Laureta L.V., and Watanabe S., 2007, Reproductive biology of mud crab Scylla serrata in Lawele Bay, Southeast Sulawesi, Indonesia, The Philippine Agricultural Scientist, 90: 88-95


Shibuno T., Nakamura Y., Horinouchi M., and Sano M., 2008, Habitat use patterns of fishes across the mangrove-seagrass-coral reef seascape at Ishigaki Island, southern Japan, Ichthyological Research, 55: 218-237


Smith D.F., Bulleid N.C., Campbell R., Higgins H.W., Rowe F., Tranter D.J., and Tranter H., 1979, Marine food-web analysis: An experimental study of demersal zooplankton using isotopically labelled prey species, Marine Biology, 54: 49-59


Sogard S.M., 1984, Utilization of meiofauna as a food source by a grassbed fish, the spotted dragonet Callionymus pauciradiatus, Marine Ecology Progress Series, 17: 183-191


Sultana R., Casareto B.E., Sohrin R., Suzuki T., Fujimura H., and Suzuki Y., 2016, Response of Subtropical Coastal Sediment Systems of Okinawa, Japan, to Experimental Warming and High pCO2, Frontiers in Marine Science, 3: 1-14


Touchette B.W., 2007, The biology and ecology of seagrasses, Journal of Experimental Marine Biology and Ecology, 350: 1-2


Tue N.T., Hamaoka H., Quy T.D., Nhuan M.T., Sogabe A., Nam N.T., and Omori K., 2013, Dual isotope study of food sources of a fish assemblage in the Red River mangrove ecosystem, Vietnam, Hydrobiologia: 1-13


Vinagre C., Máguas C., Cabral H.N., and Costa M.J., 2012, Food web structure of the coastal area adjacent to the Tagus estuary revealed by stable isotope analysis, Journal of Sea Research, 67: 21-26


Wikipedia Charybdis (genus). Accessed: 28.9.2016,


Winemiller K.O., Zeug S.C., Robertson C.R., Winemiller B.K., and Honeycutt R.L., 2011, Food-web structure of coastal streams in Costa Rica revealed by dietary and stable isotope analyses, Journal of Tropical Ecology, 27: 463-476


Youngbluth J. M., 1982, Sampling demersal zooplankton: A comparison of field collections using three different emergence traps, Journal of Experimental Marine Biology and Ecology, 61: 111-124


Zieman J.C., Macko S.A., and Mills A.L., 1984, Role of seagrasses and mangroves in estuarine food webs: Temporal and spatial changes in stable isotope composition and amino acid content during decomposition, Bulletin of Marine Science, 35: 380-392


International Journal of Marine Science
• Volume 7
View Options
. PDF(691KB)
. Online fPDF
Associated material
. Readers' comments
Other articles by authors
. Hung Manh Vu
. Beatriz Estela Casareto
. Ken-ichi Hayashizaki
. Laddawan Sangsawang
. Keita Toyoda
. Lan Dinh Tran
. Yoshimi Suzuki
Related articles
. Demersal zooplankton
. Biomass
. Stable isotope
. Mangrove
. Seagrass
. Seagrass-coral mixture
. Email to a friend
. Post a comment