Next Article in Journal
Three New and Two New Record Species of the Genus Dichaetomyia Malloch (Diptera: Muscidae) from China
Next Article in Special Issue
Differential Accumulation of Particulate Pollutants in Gills and Gastrointestinal Tracts in Sphoeroides Fish from Tropical and Subtropical Estuaries in Brazil
Previous Article in Journal
Evaluating the Toxicity of Known Western Honey Bee-Safe Insecticides in Controlling Small Hive Beetles (Aethina tumida)
Previous Article in Special Issue
Assessment of Financing for Biodiversity Conservation in Mexico: Links Between Biodiversity and Climate Change Adaptation Funds
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Diversity
Volume 17
Issue 4
10.3390/d17040231
diversity-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

Biodiversity and Seasonal Succession of Macrobenthos in Saltmarsh Habitat Adjacent to a Ship-Breaking Area

by
M. Shafiqul Islam
1,*,
Hossain Zamal
1,
Muhammad Shah Alam
2,
Md. Maheen Mahmud Bappy
3,
Abu Hena Mustafa Kamal
4,
M. Belal Hossain
3,5,* and
Takaomi Arai
6
1
Institute of Marine Sciences and Fisheries, University of Chittagong, Chittagong 4331, Bangladesh
2
Department of Zoology, University of Chittagong, Chittagong 4331, Bangladesh
3
Department of Fisheries and Marine Science, Noakhali Science and Technology University, Noakhali 3814, Bangladesh
4
Faculty of Fisheries and Food Science, Universiti Malaysia Terengganu, Kuala Nerus 21030, Terengganu, Malaysia
5
School of Engineering and Built Environment, Griffith University, Brisbane, QLD 4111, Australia
6
Environmental and Life Sciences Programme, Universiti Brunei Darussalam, Gadong BE1410, Brunei
*
Authors to whom correspondence should be addressed.
Diversity 2025, 17(4), 231; https://doi.org/10.3390/d17040231
Submission received: 6 December 2024 / Revised: 16 March 2025 / Accepted: 19 March 2025 / Published: 25 March 2025
(This article belongs to the Special Issue Socioecology and Biodiversity Conservation—2nd Edition)
Browse Figures
Versions Notes

Abstract

:
The Fauzderhat coast of Chattogram (Bangladesh) is increasingly affected anthropogenic pressures, necessitating an understanding of its ecological conditions to inform effective ecosystem management. Despite this urgency, the local succession patterns and environmental impacts on macrobenthic communities remain poorly understood. This study examines the saltmarsh bed macrobenthos in Fauzderhat, documenting 81,724 individuals from 54 species. These include ten families and twenty-two species of annelids, ten and twelve species of arthropods, and ten and eleven species of mollusks, as well as six and nine species from different phyla. Seasonality showed significantly different patterns of changes, with the number of species and abundance peaking during the monsoon (53 species) and post-monsoon (21,969) conditions, respectively, and being lowest in the post-monsoon condition (39 species) and winter (18,265 individuals). Species richness, diversity, and evenness were significantly higher in monsoon and lower in post-monsoon conditions, with the differences being only significant in the former. Cluster analysis and line graphs indicated that average species abundance was lowest post-monsoon, increased through the winter and pre-monsoon conditions, then declined again during monsoon conditions. SIMPER analysis revealed the highest dissimilarity between pre-monsoon and post-monsoon conditions while winter and post-monsoon conditions showed the lowest dissimilarity of microbenthic assemblages. Correlation coefficients showed the macrobenthos were positively correlated with soil salinity, dissolved oxygen, and pH, while they were negatively correlated with sand, Inundation Period, and nutrients. CCA showed that monsoon conditions (higher water temperature, inundation period, and tidal height) created unfavorable environments for most species, except for several species. Conversely, winter favored species like M. oligobranchia. Post-monsoon nutrient levels increased stress, reducing species presence, while pre-monsoon conditions supported balanced diversity.

1. Introduction

Macroorganisms are essential components of benthic ecosystems, contributing to energy flow, nutrient cycling, and enhanced productivity [1,2]. They inhabit a wide array of environments, including mangroves [3], seagrass beds [4], coral reefs [3], saltmarshes [5], and unvegetated mud flats [3]. Their direct dependence on environmental conditions, coupled with varying tolerance to pollutants among species, makes them key indicators of ecological health [6]. As ecosystem engineers, certain macrobenthic species shape their surroundings through activities like burrowing, which aerates sediments and influences its composition, affecting habitat structure and sympatric benthic organisms [7], while other species serve primarily as food for fish and invertebrate predators [8]. However, burrowing can also increase turbidity and resuspend pollutants, degrading water quality and impacting other organisms [9].
Saltmarshes—dynamic ecosystems bridging terrestrial and marine environments—harbor diverse microbenthic communities adapted to harsh environmental conditions [10,11], which play a crucial role in nutrient cycling. Using sediment resuspension, they enhance nutrient and dissolved gas availability in the water column, helping to maintain productivity [5]. Using aerating sediments, they support plant growth and enhance habitat complexity [12]. In turn, changes in saltmarsh vegetation can alter macrobenthic communities [13].
The Fauzderhat coast, which includes saltmarshes dominated by Porteresia coarctata [14], is highly vulnerable to flooding, storm surges [15], and pollution from the shipbreaking industry, which operates across roughly 40 shipyards in the region. This industry releases heavy metals and other toxic chemicals that severely impact water quality and fisheries, as well as the surrounding forests [16]. Pollution disrupts food chains through biomagnification, while habitat degradation threatens the ecological balance and marine biodiversity [17,18].
Being geographically and administratively part of the Sitakunda coast (Chattogram district), Fauzderhat faces pressing environmental challenges [17]. Thus, assessing its ecological status, species diversity, and seasonal patterns are crucial for informed conservation and restoration initiatives. Studying its succession patterns can provide insights into its macrobenthic biodiversity, community resilience, and recovery potential in degraded saltmarshes. Understanding the influence of environmental variables on macrobenthic communities is also critical for predicting responses to climate change and in guiding restoration efforts.
While studies on macrobenthic abundance and diversity in saltmarshes are extensive [19,20,21,22], these are limited in Bangladesh [12,23]. As biodiversity declines worldwide [24], exploring local ecosystems is increasingly crucial for conservation. Investigating macrobenthic succession and its associated environmental impacts can reveal tolerance limits, adding tailored restoration strategies to enhance biodiversity and ecosystem functionality. Therefore, this study aimed to (i) quantify the macrobenthic abundance in a coastal saltmarsh along the Chattogram coast, (ii) analyze the community structure, (iii) examine seasonal succession patterns, and (iv) evaluate the environmental impact on community diversity and succession.

2. Materials and Methods

2.1. Study Area

The Fauzderhat coast (22°23.89′–22°24.02′ N, 91°44.59′–91°44.84′ E) belongs to the Sitakunda upazila, Chattogram district (Figure 1), and suffers from high tidal ranges and frequent cyclonic activity. Water temperature ranges from 23 to 33 °C, pH ranges from 7.1 to 7.9, and salinity ranges from 1.6 to 21 ppt [25,26], and the coastline is characterized by a mix of wave-dominated sand and estuarine mud regions, with tidal pumping and fluvial fluxes significantly influencing sediment transportation processes, leading to significant erosion and accretion due to both natural processes and human activities [27,28].

2.2. Sampling Design and Collection

Samples were collected monthly during extremely low spring tides over two years divided into four seasons: monsoon (June–September), post-monsoon (October–November), winter (December–February), and pre-monsoon (March–May). Sampling was conducted across nine stations. Within (50 × 350 m2) plots, three 50 m landward-to-seaward transects were drawn along the coast (Figure 2). All stations were equidistant within the transects, with their positions and depths being estimated using a portable GPS and Topographic Abney level. Samples for macrobenthos were collected using a hand-held cylindrical core (11.5 × 15 cm2), with the corresponding labels being designated by, respectively, combining the station codes T1, T2, and T3 with S1, S2, and S3.
Triplicate samples that were 50 m long were collected from nine stations inside a (50 × 350 m2) sized plot. The replicas were located parallel to the coast from landward to seaward, being, respectively, coded as S1–S3, plus the station code (e.g., for Station 1, labels were T1S1 and T1S3) (Figure 2). The stations were set equidistant in each transect. During the fieldwork, a portable GPS and Topographic Abney level were utilized for measuring the position fixing and elevation of the sampling stations.

2.3. Sample Analysis

Five sediment replicas were collected at each station with a core (20 × 20 × 20 cm). Collected sediments were washed using a 500 μm mesh sieve [29,30], preserved in a 10% formalin solution, and stained with Rose Bengal to enhance visualization [31,32]. Preserved samples were rinsed with distilled water prior to sorting the macrobenthos into major taxonomic groups [33,34,35], which were transferred to labeled vials with 70% alcohol mixed with glycerol [29], identified to the lowest possible taxonomic level using relevant guides and manuals [33,34,35], and counted.

2.4. Data Analysis

The following univariate descriptors were used to characterize the macrobenthic assemblages: number of species, abundance (expressed as number of individuals in one square meter, ind./m2), Shannon species diversity (H’), Margalef species richness (D’), and Pielou evenness (J’) [36,37,38,39]. Data were normalized using fourth-root transformation prior to being analyzed using an analysis of variance (ANOVA) to assess for seasonal differences. Tukey’s honest significant difference test (Tukey HSD) was used to assess the responsibility for the significance of the observed differences. These analyses were performed with the SPSS (v.11.5) software. A one-way analysis of similarity (one-way ANOSIM) was conducted using PRIMER (V.7) software to assess the differences between descriptors. The total number of species and total number of individuals were counted for each season (monsoon, pre-monsoon, post-monsoon, and winter).
The similarity percentages (SIMPER) routine in PRIMER (SIMPER) was applied to determine the level of dissimilarity between the faunal assemblages of different seasons and to identify the species contributing to this dissimilarity based on the percentage contribution of individual species to average dissimilarity. Analysis was performed based on the contribution of numerically important species that cumulatively contributed 60% of total abundance. Canonical Correspondence Analysis (CCA) using the XLSTAT 2024 package was used to explore the relationships between benthic community composition and environmental variables. In total, 9 environmental factors (soil moisture, field water capacity, bulk density, particle density, porosity, (%) sand, (%) silt (%) clay, and total suspended solids) were excluded during the analysis due to avoid redundancy and ensure a more accurate representation.
Twenty-seven environmental variables (measured in triplicate; Supplementary Table S1) were analyzed for their correlation with abundance using the correlation coefficient (r) in Origin Pro v. 2024. Among the studied environmental factors, 6 environmental factors (soil moisture, soil temperature, soil pH, water transparency, field water capacity, bulk density, particle density, porosity soil organic carbon, soil organic matter, exchangeable ca, exchangeable Mg, and total suspended solids) were excluded during the analysis to avoid redundancy and ensure a more accurate representation. The season providing the most favorable environmental conditions was identified using a CCA also using the XLSTAT-2024 package.

3. Results

3.1. Abundance

The 1080 samples yielded 81,724 specimens from 48 taxa, grouped in 8 phyla (Table 1). The abundance showed significantly differed seasonally (one-way ANOSIM, global r = 0.773, p < 0.1%). Nematodes, polychaetes (Sigambra sp. and Perinereis sp.), bivalves (Mytella guyanensis, Tagelus plebeius, Macoma constricta, and Sphenia antillensis), and decapods (Uca sp.) were dominant. The most abundant species, the bivalve Tellina philippinarum, ranged from 380 ± 247 to 950 ± 789 ind./m2. T. philippinarum showed its highest abundance during winter followed by monsoon, pre-monsoon, and post-monsoon conditions. Twenty-one species exhibited higher abundance in winter, with N. indica and T. philippinarum comprising 44.69% and 35.39% of the total, respectively. Several species were absent in certain seasons. For example, Moringua raitaborua was not found during the pre-monsoon season, while S. cumanense was also absent in winter. Additionally, Phascolosoma sp. and Neanthes sp. were not observed in the post-monsoon season.

3.2. Seasonal Diversity of Macrobenthos Communities

The total number of species significantly varied seasonally, with some species thriving in specific seasons while others declined (Figure 3), being significantly lower (p < 0.05) during post-monsoon compared to monsoon conditions, winter, and pre-monsoon conditions along with the total number of individuals. Nemertea spp. (40.13%), Edwardsia jonesii (37.99%), Edwardsia tintrix (48.23%), Heteromastides sp. (48.75%), and Glauconome sculpta (19.71%), among others, were more abundant during pre-monsoon conditions. Fourteen species concentrated the highest dominances during monsoon and pre-monsoon conditions, while only B. sculpta and T. stroemi dominated during post-monsoon conditions.
Species richness ranged from 4.359 ± 0.343 to 5.189 ± 0.593 across seasons, being significantly lower in the post-monsoon season and higher in monsoon season (p < 0.05), followed by winter and pre-monsoon season. Diversity ranged from 3.342 ± 0.394 to 3.758 ± 0.467 bits, mirroring species richness, with monsoon conditions having the most diverse and relatively evenly distributed assemblages. Evenness ranged from 0.642 ± 0.041 to 3.758 ± 0.467, showing the most balanced distribution during monsoon conditions and the most imbalanced during post-monsoon conditions. While the variations in species diversity and evenness across seasons were not statistically significant, higher values were consistently recorded during monsoon conditions and lower during post-monsoon conditions.

3.3. Seasonal Succession of Macrobenthos

Seasonality strongly influenced community, with monsoon and post-monsoon conditions assemblages clustering together and becoming well distinguished for the winter/pre-monsoon. This suggests similar within-cluster similar communities and a substantial shift between them in terms of macrobenthic abundance and diversity. This strong seasonal influence could be related with differences in the degree of humidity (i.e., wetter vs. drier).
The average density was lower (1113 ± 58 ind./m2) in post-monsoon conditions and increased towards winter (4813 ± 205 ind./m2) and in pre-monsoon conditions (4519 ± 187 ind./m2), before decreasing again in monsoon and post-monsoon conditions (Figure 4). Most likely, this reflects cyclical trends in community structure in response to fluctuating environmental conditions. The average number of individuals per species was moderate (367) during monsoon conditions, with Heteromastides sp. (316) and N. indica (310), followed by Composetia sp. (163), being dominant. Likely, these are the best adapted to the freshwater inputs characterizing monsoon conditions. Heteromastides sp. showed a similarly high abundance during pre-monsoon conditions, while N. indica increased its abundance.
Numerous species experienced a reduction in abundance during post-monsoon conditions, when the average number of individuals was approximately of 338. Composetia sp. showed the highest abundance, followed by Heteromastides sp. (90 individuals) and Loimia sp. (81 individuals). Notably, Corophium sp. and S. investigatories showed significant declines during this season.

3.4. Relationships Between Environmental Variables and Macrobenthic Distribution

The abundance was positively correlated with soil salinity (r = 0.78), silt and clay (r = 0.054 and r = 0.33, respectively), dissolved oxygen (r = 0.47), and pH (r = 0.65) (Figure 5), while it was negatively correlated with sand (r = −0.31), tidal height (r = −0.52), inundation period (r = −0.40), and nutrients (r = 0.60) (Figure 5).
The first two axes of the CCA (Figure 6) explain 89.73% (F1 = 49.66%; F2 = 40.06%) of the total variance in macrobenthic distribution across seasons. During monsoon conditions (upper right quadrant), higher water temperature, inundation period, and tidal height, together with moderate sediment and water salinities and organic carbon were observed. These conditions led to increased water influx and mixing that were unfavorable for most species. However, species such as G. sculpta, Neanthes sp., Nemertea spp., Heteromastides sp., E. jonesii, and Prionchulus sp. showed strong associations with this season. In contrast, winter (lower left quadrant, Figure 6) showed a distinct community structure. Lower water temperatures and depths provided favorable conditions for many species, including M. oligobranchia, T. rivalis, Phascolosoma sp., and Hesionidae sp.
Post-monsoon conditions (upper left quadrant, Figure 6) were characterized by high nutrient levels (exchangeable K, available Phosphorus, total Nitrogen) and high dissolved oxygen. However, the increased bottom temperature, and bottom and water pH give rise to more stressful conditions, resulting in the lower presence of species such as L. melanostoma, Loimia sp., Sipunculus sp., and Composetia sp. Pre-monsoon conditions (lower right quadrant, Figure 6) supported species like Capitella sp., Prionchulus sp., and Heteromastides sp., with the fewer closely associated environmental factors suggesting balanced conditions. This appears to be a transition season, placed between the more favorable winter and the less favorable post-monsoon and monsoon season, with the moderate environmental conditions overall favoring species diversity.
The transition from less abundant post-monsoon conditions to more abundant winter and pre-monsoon conditions strongly suggest that macrobenthic dynamics are driven by seasonal environmental factors. Species like Capitella sp. showed strict seasonal preferences (i.e., pre-monsoon conditions) while species like Sipunculus sp.—located near the plot center (Figure 6)—showed broader tolerance.

4. Discussion

4.1. Abundance of Macrobenthos

The taxa diversity in this study was lower than in the Bohai Sea, northwest India (14 phyla), the northern Yellow Sea (7 phyla, 153 species, 301–598 specimens), and the Ulleung Basin (262 species) [2,40,41]. This lower diversity may be attributed to the high levels of pollutants and habitat degradation along the Fauzderhat coast. In contrast, the diversity appears to be higher than along the Cox’s Bazar coast, were only six major groups (gastropoda, bivalvia, polychaeta, oligochaeta, Sipuncula, and crustacea) were reported [41]. Most likely, this could be due to differences in human impact, sediment types, and water quality. However, different methodologies—such as sampling area size, sampling frequency, and techniques (e.g., grabs vs. cores)—could also contribute to the abundance and diversity discrepancies. The dominance of nematodes, polychaetes, and bivalves in our study aligns with the previously reported prevalence of polychaetes and bivalves found in other studies [2,41,42]. However, crustaceans and mollusks dominated the Malaysian coastal waters [43], while polychaetes, isopods, and gastropods dominate the Brazilian saltmarshes [44]. These differences could be linked to local environmental factors and variations in saltmarsh vegetation, where polychaetes, mollusks, and crustaceans often tend to be dominant [2,41,43,44]. The adaptability of polychaetes to varying environmental conditions, such as salinity and temperature [45,46], likely explain their prevalence, underscoring their value as bioindicators for environmental health assessments. Similarly, the favorable salinity and temperature conditions could also support the prevalence of mollusk and crustacean microbenthic species [12].

4.2. Seasonal Diversity

The two species (N. indica and T. philippinarum) constituted a substantial proportion (80.08%) of the overall abundance among the 21 species that were more abundant in winter. This indicated that these two species are especially dominant or well-suited to winter conditions in the examined area. This also suggests that these species may thrive under colder temperatures or seasonal nutrient conditions, potentially benefiting from reduced interspecific competition in contrasts with the data from Minicoy Island, where a lower diversity was recorded during the monsoon season [47]. The monsoon season also favored species such as Sipunculus sp. and Loimia sp., while polychaetes may represent up to 64% of the total benthos during the monsoon season [48], when an increasing sedimentation and available organic matter may create favorable feeding and breeding conditions. We have found several taxa to be more dominant during the pre-monsoon season (i.e., Nemertea spp., E. jonesii, E. tintrix, Heteromastides sp., and G. sculpta). In contrast, only polychaetes were dominant during the pre-monsoon season in the Naf River estuary, where the macrobenthic abundances were overall higher (2972 ± 1994 ind./m2) [48] compared to Fauzderhat. Therefore, warming waters and increased food availability during the pre-monsoon season seem to create optimal growth conditions favoring the multiple taxa dominance observed in Fauzderhat. Similarly, a study in a tropical estuary linked post-monsoon season declines to increased freshwater inflow reducing salinity [49]. The maximum number of species and individuals during the monsoon season and winter, respectively, in contrast with the higher diversity during the post-monsoon season in a subtropical mangrove estuary [50]. Accordingly, the dominance of a particular species during particular seasons appears to be influenced by environmental factors such as temperature, salinity, and food availability, which shape habitat suitability and competition dynamics.
Species richness was lower in the post-monsoon season and higher in the monsoon season, in contrast with previous reports of peaking in summer and lowering in winter [51]. The monsoon season had the most diverse community, in contrast with other studies showing a diversity of 2.1 bits, significant seasonal changes, and higher values in shallow waters, particularly in summer [2], or ranging from 2.55 to 2.92 bits [51]. The observed seasonal changes in evenness contrast with the uniform diversities and minor evenness fluctuations across seasons found across the western Indian coasts [52]. These differences likely arise from habitat type (shallow vs. deep water) and varying environmental conditions, such as temperature and salinity, influencing species distribution.

4.3. Seasonal Succession

The marked seasonality found in the macrobenthic community in the Sitakundu coastal saltmarsh could be caused by variations in hydrodynamic conditions, salinity, and organic matter supply between the wet (monsoon) and dry seasons. The wet season has more freshwater inputs and increasing sedimentation rates, which altered habitat conditions, leading to lower diversity and density, whereas the dry season ensured more stable salinity and oxygen levels, facilitating recruitment and growth. Additionally, monsoonal disruptions and intermittent flooding likely influence species composition by reshaping substrate topography and food sources. In return, the communities were less diverse in November and October and more diverse in February at Merchang lagoon [53], while summer conditions significantly affected species diversity and abundance in the northern Gulf of Mexico [54], leading to community structure shifts similar to those observed in Fauzderhat. Environmental factors, such as nutrient availability and hydrodynamic conditions, strongly influenced community succession patterns [55] as they occurred in Fauzderhat, but also in the Naf River estuary, where the abundance was higher during the pre-monsoon season compared to the monsoon season [48]. The reduced abundance of Corophium sp. and S. investigatories during the post-monsoon season was likely caused by the habitat being altered by increased sedimentation rates [56]. Seasonal variations in precipitation, which directly influence salinity levels and hence impact water density, seem to be a primary factor in the observed patterns of species abundance. N. indica demonstrated peak abundance in winter, with 1039 individuals documented, followed by a small reduced count of 915 individuals in the pre-monsoon period. This periodic fluctuation in abundance presumably indicates the species’ sensitivity to salinity variations, ultimately leading to a shift in species’ dominance across the seasons.
Winter’s lower temperature and freshwater inflow gives rise to more stable conditions for macrobenthos [57], while water temperature, total phosphorus, and total nitrogen critically influence the abundance [1], and stable environments and higher food availability positively influence diversity [50]. The strong seasonal differences shown by the macrobenthos supports the Fauzderhat saltmarsh as being a dynamic ecosystem, where the cyclical domination of different species at different times of the year emerges as a key indicator of ecosystem succession. Different environmental conditions likely affected species presence and abundance, which resulted in significant differences in community composition and structure, as previously reported in a river-connected floodplain lake [41] and other macrobenthic communities [55,58]. Shifts in community structure across seasons affected abundance, dominance, and diversity, likely being driven by environmental changes and species interactions.

4.4. Environmental Variables and Their Effects

The correlation analysis indicated an overall good adaptation of macrobenthos to more saline conditions, as shown in previous studies in which species richness was also benefited [1,12]. Increasing sand contents has been suggested to lead to decreasing habitat complexity and resource availability, thus negatively affecting macrobenthic diversity and abundance compared to the richer organic matter and nutrient content provided by muddy or silty substrates, which tend to support more diverse communities [4,59,60]. Macrobenthos showed a preference for well-oxygenated neutral-to-slightly alkaline conditions, as found in the Heihe River Basin [1]. In contrast, the tidal height and inundation periods apparently had a detrimental effect on organism performances. Excessive increases in nutrient loads may lead to eutrophication, algal blooms, and subsequent hypoxia, as it occurs during the monsoon season [61,62]. This may adversely affect the most sensitive species, leading to altered community structure and succession, likely explaining the strong negative correlation between nutrients and abundance and favoring pollution-tolerant species over those less adapted to such environments [60].
The results of the CCA align with previous studies, in which elevated turbidity and fluctuating pH led to reduced diversity [61], while winter’s colder temperatures and increased habitat stability fostered higher species richness, likely by lowering metabolic rates [61,63]. Despite nutrient enrichment can initially help in supporting diverse communities, the pre-monsoon season’s extreme soil temperatures and pH fluctuations often created unfavorable conditions for macrobenthic organisms [61,62]. The post-monsoon season showed extreme environmental fluctuations with lower presence of species and the pre-monsoon season was a transition period favoring species diversity. Stable temperatures and nutrient levels associated with the transitional periods often foster more diverse communities compared to the periods with more extreme fluctuations [62,63]. Seasonal assemblage structure shifts appear to be driven by nutrient availability and physical parameters, combined with species-specific adaptations to the different seasonal conditions within the saltmarsh ecosystem.

5. Conclusions

This study investigates the abundance, diversity, and seasonal dynamics of macrobenthic communities in an anthropically influenced coastal ecosystem. Of the 53 taxa recorded, nematodes, polychaetes, decapods, and bivalves dominated at different seasons. All of our different analytical approaches showed distinct macrobenthic successional patterns reflecting ecological process dynamics, with some species declining while others becoming dominant. Bottom salinity and water depth, dissolved oxygen, and pH proved to be the key variables shaping macrobenthic abundance. The evident seasonal succession pattern at Fauzderhat saltmarsh underscores the resilience of this particular ecosystem, prompting its ability to recover from anthropic disturbances—such as habitat modification—and offering valuable insights for the conservation and sustainable management of coastal biodiversity.

Supplementary Materials

The following supporting information can be downloaded at: https://www.mdpi.com/article/10.3390/d17040231/s1, Supplementary Table S1. Average (±SD) values of different environmental factors of the Fauzderhat area in the Chittagong coast in different seasons of two years of sampling sessions.

Author Contributions

Conceptualization, M.S.I. and H.Z.; Methodology, M.S.A., A.H.M.K. and M.B.H.; Software, M.M.M.B.; Validation, A.H.M.K.; Formal analysis, T.A.; Investigation, A.H.M.K.; Resources, M.M.M.B.; Data curation, H.Z.; Writing – original draft, M.S.I. and M.M.M.B.; Writing – review & editing, M.B.H. and T.A.; Supervision, H.Z. and M.S.A. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by Universiti Brunei Darussalam research grant number UBD/RSCH/1.4/FICBF(b)/2023/057.

Institutional Review Board Statement

Not applicable for studies not involving humans.

Data Availability Statement

Data is contained within the article and Supplementary Materials.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Wang, Y.; Liu, J.J.; Li, B.L.; Liu, W.; Zuo, Y.F.; Kong, D.X.; Zhu, J.L. Relationships between characteristics of macrobenthic assemblages and environmental variables in the Heihe River Basin, China. AQUA—Water Infrastruct. Ecosyst. Soc. 2021, 70, 710–730. [Google Scholar] [CrossRef]
  2. Kim, S.L.; Kang, S.M.; Lee, H.G.; Han, G.H.; Yu, O.H. Species Diversity and Community Structure of Macrobenthos in the Ulleung Basin, East Sea, Republic of Korea. J. Mar. Sci. Eng. 2023, 11, 92. [Google Scholar] [CrossRef]
  3. Armenteros, M.; Saladrigas, D.; González-Casuso, L.; Estevez, E.D.; Kowalewski, M. The role of habitat selection on the diversity of macrobenthic communities in three gulfs of the Cuban Archipelago. Bull. Mar. Sci. 2018, 94, 249–268. [Google Scholar]
  4. Ji, Y.; Song, B.; Xu, J.; Jiang, S.; Chen, L.; Li, B. Distribution and influencing factors of macrobenthos on three seagrass beds in the intertidal zone of Shandong province, China. Front. Mar. Sci. 2024, 11, 1349131. [Google Scholar] [CrossRef]
  5. Ullah, M.A.; Hossain, M.S.; Hossain, M.B.; Rahman, M. Belal Hossain, and Mahbubur Rahman. Intertidal variation of macrobenthos in a saltmarsh habitat, Noakhali coast, Bangladesh. Egypt. J. Aquat. Biol. Fish. 2020, 24, 377–390. [Google Scholar]
  6. Pawhestri, S.W.; Hidayat, J.W.; Putro, S.P. Assessment of water quality using macrobenthos as bioindicator and its application on Abundance-Biomass Comparison (ABC) curves. Int. J. Sci. Eng. 2014, 8, 84–87. [Google Scholar]
  7. Gage, J.D. Macrobenthos en Encyclopedia of Ocean Science; Scottish Association for Marine Science: Oban, UK, 2001; Volume 3, pp. 1505–1515. [Google Scholar]
  8. Jia, K.; Tang, Y.; Liu, Q.; Zhang, R.; Liao, Y.; Shou, L.; Zeng, J.; Chen, Q.; Chen, J. Spatial and temporal distribution of macrobenthos communities and their relationship with secondary front in Hangzhou Bay. Front. Mar. Sci. 2022, 9, 1037287. [Google Scholar] [CrossRef]
  9. Muskananfola, M.R.; Purnomo, P.W.; Sulardiono, B. Impact of environmental factors on macrobenthos distribution and abundance in mangrove ecosystems on the Northern Coast of Java. AACL Bioflux 2020, 13, 2745–2756. [Google Scholar]
  10. Touchette, B.W.; Schmitt, S.R.; Moody, J.W. Enhanced thermotolerance of photosystem II by elevated pore-water salinity in the coastal marsh graminoid Sporobolus pumilus. Aquat. Biol. 2020, 29, 111–122. [Google Scholar] [CrossRef]
  11. Vahsen, M.L.; Kleiner, H.S.; Kodak, H.; Summers, J.L.; Vahsen, W.L.; Blum, M.J.; Megonigal, J.P.; McLachlan, J.S. Complex eco-evolutionary responses of a foundational coastal marsh plant to global change. New Phytol. 2023, 240, 2121–2136. [Google Scholar] [CrossRef]
  12. Mely, S.S.; Hossain, M.B.; Rahman, M.; Albeshr, M.F.; Arai, T. Changes of Macrobenthic Diversity and Functional Groups in Saltmarsh Habitat under Different Seasons and Climatic Variables from a Subtropical Coast. Sustainability 2023, 15, 7075. [Google Scholar] [CrossRef]
  13. Gandini, L.J.R.; Funk, F.A.; Pratolongo, P.D. Pratolongo. Change in the community structure and organic carbon content of meio-and macrobenthos between tidal flat and salt marsh areas colonized by Spartina alterniflora in the Bahía Blanca estuary (SW Atlantic). Sci. Mar. 2023, 87, 3. [Google Scholar]
  14. Islam, M.S.; Imran, M.A.; Mandol, S.; Bhuyan, M.S. Restoration of saltmarsh as mitigative measure of climate change impact at Chittagong coastal area of Bangladesh. Clim. Change 2016, 2, 313–329. [Google Scholar]
  15. Miah, J.; Hossain, K.T.; Hossain, M.A.; Najia, S.I. Assessing coastal vulnerability of Chittagong District, Bangladesh using geospatial techniques. J. Coast. Conserv. 2020, 24, 66. [Google Scholar]
  16. Fakhruddin, A.N.M.; Talukdar, M.I.; Hossain, M.A. Environmental impacts of ship breaking and recycling industry of Sitakunda, Chittagong, Bangladesh. Adv. Nat. Sci. 2015, 8, 51–58. [Google Scholar]
  17. Hossain, M.S.; Fakhruddin, A.N.M.; Chowdhury, M.A.Z.; Gan, S.H. Impact of ship-breaking activities on the coastal environment of Bangladesh and a management system for its sustainability. Environ. Sci. Policy 2016, 60, 84–94. [Google Scholar]
  18. Kutub, J.R.; Falgunee, N.; Nawfee, S.M.; Rabby, Y.W. Ship breaking industries and their impacts on the local people and environment of coastal areas of Bangladesh. Hum. Soc. Stud. 2017, 6, 35–58. [Google Scholar]
  19. Li, S.; Cui, B.; Xie, T.; Shao, X.; Zhang, M. Consequences and implications of anthropogenic desalination of salt marshes on macrobenthos. CLEAN–Soil Air Water 2016, 44, 8–15. [Google Scholar]
  20. Lee, H.G.; Yoon, K.T.; Park, H.S.; Hong, J.S.; Lee, J.H. The influence of environmental variables on distribution of macrobenthic community in salt marsh vegetation in Donggeomdo, Ganghwa on the west coast of Korea. Ocean. Polar Res. 2016, 38, 115–128. [Google Scholar] [CrossRef]
  21. Qiu, D.; Yan, J.; Ma, X.; Gao, F.; Wang, F.; Wen, L.; Bai, J.; Cui, B. How vegetation influence the macrobenthos distribution in different saltmarsh zones along coastal topographic gradients. Mar. Environ. Res. 2019, 151, 104767. [Google Scholar]
  22. Santos, T.M.T.; Rabelo, D.M.L.; Beasley, C.R.; Braga, C.F. Vertical distribution of macrobenthic community of tropical saltmarshes on the Amazon coast. Reg. Stud. Mar. Sci. 2020, 40, 101536. [Google Scholar] [CrossRef]
  23. Islam, M.S.; Pervez, A.; Asseri, A.H.; Al-Mutair, M.; Sumon, M.A.A.; Taleb, M.A.; Ashik, A.A.; Rahman, M.A.; Molla, M.H.R. Diversity and seasonal succession of resident and migratory macrobenthic fauna of saltmarsh restoration site at Sonadia Island, Cox’s Bazar, Bangladesh. Reg. Stud. Mar. Sci. 2022, 53, 102460. [Google Scholar] [CrossRef]
  24. Haque, M.M.; Sharif, A.S.M.; Ahmed, M.K.; Anwar, F.; Rani, S.; Molla, M.H.R.; Khan, M.I. Distribution and diversity of macrobenthos in Sangu River, Bangladesh. Dhaka Univ. J. Earth Environ. Sci. 2020, 9, 27–34. [Google Scholar] [CrossRef]
  25. Talukder, A.; Mallick, D.; Hasin, T.; Anka, I.Z.; Hasan, M.M. Spatio-temporal variability in hydro-chemical characteristics of coastal waters of Salimpur, Chittagong along the Bay of Bengal. J. Fish. 2016, 4, 335–344. [Google Scholar]
  26. Islam, S.S.; Tanim, A.H.; Mullick, M.R.A. Vulnerability assessment of Bangladesh coastline using Gornitz method. In Water, Flood Management and Water Security Under a Changing Climate: Proceedings from the 7th International Conference on Water and Flood Management; Springer International Publishing: New York, NY, USA, 2020; pp. 301–313. [Google Scholar]
  27. Barua, D.K. The coastline of Bangladesh—An overview of processes and forms. In Coastal Zone’91; ASCE: Preston, VA, USA, 1991; pp. 2284–2301. [Google Scholar]
  28. Khan, M.S.; Das, J.; Kabir, M.H. Monitoring coastline changes in the coastal belt of chittagong in Bangladesh Using GIS and remote sensing. Asian J. Geogr. Res. 2019, 2, 1–13. [Google Scholar]
  29. Tagliapietra, D.; Sigovini, M. Benthic fauna: Collection and identification of macrobenthic invertebrates. Terre Et Environ. 2010, 88, 253–261. [Google Scholar]
  30. Enge, A.J.; Wanek, W.; Heinz, P. Preservation effects on isotopic signatures in benthic foraminiferal biomass. Mar. Micropaleontol. 2018, 144, 50–59. [Google Scholar] [CrossRef]
  31. Shiozaki, T.; Itoh, F.; Hirose, Y.; Onodera, J.; Kuwata, A.; Harada, N. A DNA metabarcoding approach for recovering plankton communities from archived samples fixed in formalin. PLoS ONE 2021, 16, e0245936. [Google Scholar]
  32. Rahman, M.K.; Hossain, M.B.; Majumdar, P.R.; Mustafa, M.G.; Abu Noman, M.; Albeshr, M.F.; Bhat, E.A.; Arai, T. Macrobenthic assemblages, distribution and functional guilds from a freshwater-dominated tropical estuary. Diversity 2022, 14, 473. [Google Scholar] [CrossRef]
  33. Carpenter, K.E.; De Angelis, N. The Living Marine Resources of the Eastern Central Atlantic. Volume 1: Introduction, Crustaceans, Chitons, and Cephalopods; FAO: Rome, Italy, 2014. [Google Scholar]
  34. Carpenter, K.E.; Niem, V.H. (Eds.) The Living Marine Resources of the Western Central Pacific. Volume 1. Seaweeds, Corals, Bivalves and Gastropods; FAO: Rome, Italy, 1998; p. xiv+-686. [Google Scholar]
  35. Carpenter, K.E. Introduction, Molluscs, Crustaceans, Hagfishes, Sharks, Batoid Fishes and Chimaeras; Food and Agriculture Organization of the United Nations: Rome, Italy, 2002. [Google Scholar]
  36. Welch, P.S. Limnological Methods; McGraw-Hill: New York, NY, USA, 1948. [Google Scholar]
  37. Shannon, C.E. A mathematical theory of communication. Bell Syst. Tech. J. 1948, 27, 379–423. [Google Scholar] [CrossRef]
  38. Margalef, R. Information theory in ecology. Real Acad. De Cienc. Y Artes De Barc. Traslation Ser. 1973, 2609, 1–140. [Google Scholar]
  39. Pielou, E.C. The measurement of diversity in different types of biological collections. J. Theor. Biol. 1966, 13, 131–144. [Google Scholar] [CrossRef]
  40. Sukumaran, S.; Vijapure, T.; Mulik, J.; Ridha, H. Marine macrobenthos of NorthWest India-reviewing the known and unknown. Front. Mar. Sci. 2021, 8, 671245. [Google Scholar] [CrossRef]
  41. Li, F.; Ma, Y.; Song, X.; Li, S.; Zhang, X.; Wang, X.; Wang, T.; Sun, Z. Community structure and ecological quality assessment of macrobenthos in the coastal sea areas of Northern Yantai, China. Front. Mar. Sci. 2022, 9, 989034. [Google Scholar] [CrossRef]
  42. Abu Hena, M.K.; Akhtar, A.; Khan, M.A.A.; Uddin, S.A.; Rezowan, M. Community structure of macro benthos in an estuarine salt marsh habitat at Cox’s Bazar. Bangladesh J. Mar. Sci. 2009, 1, 119–132. [Google Scholar]
  43. Chowdhury, A.J.K.; John, A.; Aqilah, N.S.; Abdullah, R.; Salihah, N.T.; Basir, K.H.; Marsal, C. Macrobenthic community towards sustainable aquatic ecosystem: A systematic review along the coastal waters of Malaysia. Geol. Ecol. Landsc. 2024, 8, 57–70. [Google Scholar] [CrossRef]
  44. Braga, C.F.; Beasley, C.R.; Isaac, V.J. Effects of plant cover on the macrofauna of Spartina marshes in northern Brazil. Braz. Arch. Biol. Technol. 2009, 52, 1409–1420. [Google Scholar] [CrossRef]
  45. Musale, A.S.; Desai, D.V. Distribution and abundance of macrobenthic polychaetes along the South Indian coast. Environ. Monit. Assess. 2011, 178, 423–436. [Google Scholar] [CrossRef]
  46. Kim, S.L.; Lee, H.G.; Yu, O.H. Correlation between rocky reefs and surrounding benthic habitats: Distribution and diversity patterns of polychaetes in the macrobenthic community in the East Sea of South Korea. J. Sea Res. 2021, 174, 102083. [Google Scholar] [CrossRef]
  47. Dalia Susan, V.; Satheesh Kumar, P.; Pillai, N.G.K. Biodiversity and seasonal variation of benthic macrofauna in Minicoy Island, Lakshadweep, India. Acta Oceanol. Sin. 2014, 33, 58–73. [Google Scholar] [CrossRef]
  48. Noman, A.; Mamunur, R.; Islam, M.S.; Hossain, M.B. Spatial and seasonal distribution of intertidal macrobenthos with their biomass and functional feeding guilds in the Naf River estuary, Bangladesh. J. Oceanol. Limnol. 2019, 37, 1010–1023. [Google Scholar]
  49. Lowe, V.; Frid, C.L.; Venarsky, M.; Burford, M.A. Responses of a macrobenthic community to seasonal freshwater flow in a wet-dry tropical estuary. Estuar. Coast. Shelf Sci. 2022, 265, 107736. [Google Scholar]
  50. Khatun, B.; Jewel, A.S.; Haque, A.; Akter, S.; Hossain, M.B.; Albeshr, M.F.; Arai, T. Seasonal pattern of taxonomic diversity and functional groups of macro-benthos from a sub-tropical mangrove estuary. J. Mar. Sci. Eng. 2023, 11, 1453. [Google Scholar] [CrossRef]
  51. Sharmin, S.; Rahman, S.; Naser, M.; Hoque, S. Macro benthic fauna in relation to limnological variables in a migratory bird visiting lake at Jahangirnagar University, Bangladesh. J. Biodivers. Conserv. Bioresour. Manag. 2018, 4, 99–106. [Google Scholar]
  52. Pawar, P.R.; Kulkarni, B.G. Diversity indices of selected macrobenthos in Karanja Creek (District-Raigad), Maharashtra, west coast of India. J. Indian Fish. Assoc. 2007, 34, 1–9. [Google Scholar]
  53. Hussin, W.M.R.W.; Ab Lah, R. Community structure and taxonomic diversity of macrobenthic communities in Merchang lagoon, Malaysia. Aquac. Aquar. Conserv. Legis. 2020, 13, 3593–3604. [Google Scholar]
  54. Shivarudrappa, S.; Briggs, K. Macrobenthos community succession in the northern Gulf of Mexico hypoxic regions: Testing the Pearson-Rosenberg model. J. Mar. Res. 2017, 75, 18–46. [Google Scholar]
  55. Pacheco, A.S.; Laudien, J.; Thiel, M.; Oliva, M.; Arntz, W. Succession and seasonal variation in the development of subtidal macrobenthic soft-bottom communities off northern Chile. J. Sea Res. 2010, 64, 180–189. [Google Scholar]
  56. Matin, A.; Hossain, M.B.; Iqbal, M.; Billah, M.M.; Asif, A.A.; Billah, M.M. Diversity and abundance of Macrobenthos in a subtropical estuary, Bangladesh. Species 2018, 19, 140–150. [Google Scholar]
  57. Kosari, S.; Nadushan, R.M.; Faremi, R.; Khanghah, K.E.; Mashinchian, A. Macrobenthos as bioindicator of ecological status in the Yekshabe creek-estuary, Persian Gulf. Iran. J. Fish. Sci. 2011, 20. [Google Scholar] [CrossRef]
  58. Gerami, M.H.; Patimar, R.; Negarestan, H.; Jafarian, H.; Mortazavi, M.S. Temporal variability in macroinvertebrates diversity patterns and their relation with environmental factors. Biodiversitas J. Biol. Divers. 2016, 17. [Google Scholar] [CrossRef]
  59. Dutertre, M.; Hamon, D.; Chevalier, C.; Ehrhold, A. The use of the relationships between environmental factors and benthic macrofaunal distribution in the establishment of a baseline for coastal management. ICES J. Mar. Sci. 2013, 70, 294–308. [Google Scholar] [CrossRef]
  60. Shi, Y.; He, Y.; Shin, P.K.; Guo, Y.; Zhang, G.; Wen, Y.; Zhang, G.; Xu, W.; Sun, J. Responses of biological traits of macrobenthic fauna to a eutrophication gradient in a semi-enclosed bay, China. Mar. Environ. Res. 2023, 189, 106072. [Google Scholar]
  61. Das Ghosh, B.; Debnath, S.; Sarkar, U.K.; Das, B.K.; Puthiyottil, M.; Johnson, C.; Karnatak, G. Ecological assessment of a subtropical floodplain wetland of the Ganga basin in the context of changing climate using GIS tools. J. Water Clim. Change 2023, 14, 4220–4235. [Google Scholar]
  62. Joseph, S.J.P.; Gunasekaran, P.D.; Subramani, N. Influence of environmental parameters on the community structure of phytoplankton from river confluence of Cuddalore, Tamil Nadu, India. Environ. Adv. 2022, 7, 100170. [Google Scholar]
  63. Molina, A.; Duque, G.; Cogua, P. Influences of environmental conditions in the fish assemblage structure of a tropical estuary. Mar. Biodivers. 2020, 50, 5. [Google Scholar]
Diversity 17 00231 g001
Figure 1. The location of the study area shows nine sampling stations.
Figure 1. The location of the study area shows nine sampling stations.
Diversity 17 00231 g001
Diversity 17 00231 g002
Figure 2. Sampling design showing the studied stations and spots.
Figure 2. Sampling design showing the studied stations and spots.
Diversity 17 00231 g002
Diversity 17 00231 g003
Figure 3. (a) Seasonal variation in species richness (Margalef, d), species diversity (Shannon, H’) and evenness (Pielou, J’), (b) seasonal variation in macrobenthic species number, and (c) seasonal variation in macrobenthic individuals observed in the Fauzderhat area of Chattogram. Different letters on the top of the bars indicate significant differences among the seasons.
Figure 3. (a) Seasonal variation in species richness (Margalef, d), species diversity (Shannon, H’) and evenness (Pielou, J’), (b) seasonal variation in macrobenthic species number, and (c) seasonal variation in macrobenthic individuals observed in the Fauzderhat area of Chattogram. Different letters on the top of the bars indicate significant differences among the seasons.
Diversity 17 00231 g003
Diversity 17 00231 g004
Figure 4. Distinct patterns of macrobenthic abundance in the four different seasons. Community composition significantly differed between monsoon and post-monsoon conditions (Table 2).
Figure 4. Distinct patterns of macrobenthic abundance in the four different seasons. Community composition significantly differed between monsoon and post-monsoon conditions (Table 2).
Diversity 17 00231 g004
Diversity 17 00231 g005
Figure 5. Correlation coefficients between macrobenthic abundance and environment: (a) sediment physio-chemical factors; (b) water factors; (c) tidal changes; (d) nutrients.
Figure 5. Correlation coefficients between macrobenthic abundance and environment: (a) sediment physio-chemical factors; (b) water factors; (c) tidal changes; (d) nutrients.
Diversity 17 00231 g005
Diversity 17 00231 g006
Figure 6. Canonical correspondence analysis between macrobenthic abundance and environmental factors. Seasons (monsoon, pre-monsoon, post-monsoon, and winter) are indicated in blue color.
Figure 6. Canonical correspondence analysis between macrobenthic abundance and environmental factors. Seasons (monsoon, pre-monsoon, post-monsoon, and winter) are indicated in blue color.
Diversity 17 00231 g006
Table 1. Abundance (ind./m2) of macrobenthos in the saltmarsh during the monsoon, post-monsoon, winter, and pre-monsoon seasons.
Table 1. Abundance (ind./m2) of macrobenthos in the saltmarsh during the monsoon, post-monsoon, winter, and pre-monsoon seasons.
Taxon ID No.TaxaMonsoonPost-MonsoonWinterPre-Monsoon
01Nemertea spp. Max Johann Sigismund Schultze, 185185 ± 5131 ± 6 b63 ± 10102 ± 40 a
02Scopimera investigatoris Alcock, 190034 ± 20 a5 ± 2 b23 ± 923 ± 6
03Tellina philippinarum Hanley, 1844687 ± 440380 ± 247950 ± 789667 ± 399
04Micronephthys oligobranchia Southern, 192180 ± 46 a4 ± 4 a278 ± 81 b208 ± 95 b
05Edwardsia jonesii Seshaiya & Cuttress, 1969125 ± 46 a16 ± 4 b112 ± 75155 ± 87 a
06Edwardsia tintrix Annandale, 191593 ± 40 b8 ± 4 b147 ± 98 a231 ± 33 a
07Sipunculus sp. Linnaeus, 1766128 ± 64 a36 ± 16 b77 ± 4573 ± 28
08Heteromastides sp. Augener, 1914316 ± 14990 ± 61 b229 ± 174 b604 ± 380 a
09Littoraria melanostoma Gray, 183926 ± 8 a 10 ± 8 b10 ± 9 b14 ± 9
10Nerita violacea Gmelin, 17916 ± 3 a2 ± 1 b2 ± 2 b4 ± 3
11Composetia sp. Hartmann-Schröder, 1985163 ± 73 b183 ± 100 b416 ± 95 a80 ± 22 b
12Diopatra sp. Audouin & Milne Edwards, 18336 ± 6 b8 ± 3 b34 ± 24 a9 ± 4 b
13Ocypode ceratophthalma Pallas, 17725 ± 51 ± 22 ± 24 ± 3
14Prionchulus sp. Nathan Augustus Cobb in 191641 ± 1110 ± 2 b43 ± 19114 ± 122 a
15Alicella sp. Chevreux, 18998 ± 8 a7 ± 1 a7 ± 6 a1 ± 1 b
16Diptera larvae4 ± 41 ± 2 b10 ± 8 a4 ± 2
17Dendronereis sp. Peters, 18543 ± 3 b2 ± 2 b4 ± 4 b12 ± 8 a
18Belba sculpta Mihelčič, 19574 ± 4 b15 ± 6 a7 ± 3 b2 ± 2 b
19Moringua raitaborua Hamilton, 18221 ± 10 ± 01 ± 11 ± 1
20Siphonosoma cumanense Keferstein, 186716 ± 12 a0 ± 0 b0 ± 0 b2 ± 2 b
21Glauconome sculpta G. B. Sowerby III, 189455 ± 22 b48 ± 20 b48 ± 12 b128 ± 72 a
22Loimia sp. Malmgren, 1866128 ± 74 a81 ± 12 b120 ± 65 a66 ± 57 b
23Littorina undulata J. E. Gray, 18394 ± 35 ± 46 ± 54 ± 2
24Capitella sp. Blainville, 182831 ± 42 b11 ± 5 b69 ± 53 b594 ± 832 a
25Terebellides sp. Sars, 183566 ± 6713 ± 11 b143 ± 82 a149 ± 61 a
26Venitus dentipes Lucas in Guérin, 183615 ± 18 a1 ± 1 b8 ± 8 a12 ± 9 a
27Corophium sp. Latreille, 180624 ± 21 a2 ± 2 b20 ± 6 a7 ± 7 b
28Namalycastis indica Southern, 1921310 ± 32361 ± 45 b1039 ± 663 a915 ± 690
29Namalycastis fauveli Nageswara Rao, 19817 ± 72 ± 2 b15 ± 9 a12 ± 12 a
30Lumbrineris pseudobifilaris Fauvel, 19321 ± 2 b4 ± 34 ± 511 ± 15 a
31Polydora sp. Oken, 18154 ± 2 b4 ± 2 b17 ± 1 a9 ± 8
32Glycinde oligodon Southern, 19211 ± 11 ± 13 ± 23 ± 4
33Glycera lancadivae Schmarda, 18610 ± 0 b1 ± 1 b27 ± 25 a2 ± 4 b
34Phascolosoma sp. Leuckart, 182811 ± 13 b0 ± 10 b481 ± 305 a110 ± 40 b
35Dasybranchus sp. Grube, 18501 ± 1 b1 ± 1 b4 ± 4 a0 ± 0 b
36Nemalycastis indica Southern, 19211 ± 1 b0 ± 0 b2 ± 1 a0 ± 0 b
37Culicoides sp. Latreille, 18092 ± 30 ± 01 ± 11 ± 2
38Sabellidae sp. Latreille, 18251 ± 1 b0 ± 0 b7 ± 1 a1 ± 11 a
39Sphaeroma sp. Bosc, 18016 ± 7 a0 ± 0 b3 ± 3 a1 ± 1 b
40Gammarus sp. Fabricius, 17755 ± 4 a1 ± 21 ± 1 b1 ± 1 b
41Hesionidae sp. Grube, 18504 ± 4 b2 ± 3 b35 ± 39 a15 ± 6
42Pterynotus elongatus [Lightfoot], 17863 ± 20 ± 01 ± 12 ± 1
43Procellio spinicornis Thomas Say, 18185 ± 4 a0 ± 0 b1 ± 1 b1 ± 1 b
44Portunus sp. Weber, 17959 ± 6 a0 ± 0 b11 ± 17 a0 ± 0 b
45Urothoe lacteal Dana, 18521 ± 1 b0 ± 0 b14 ± 3 a2 ± 1 b
46Stenothyra deltae W. H. Benson, 1837 4 ± 3 b13 ± 7 a5 ± 5 b3 ± 3 b
47Tanysyphon rivalis Benson, 185817 ± 7 b22 ± 8 b174 ± 149 a16 ± 4 b
48Laevicaulis alte André Étienne d’Audebard de Ferussac, 18222 ± 22 ± 21 ± 12 ± 4
Note: Different superscripts in the same row denote statistically significant different subsets according to Tukey’s HSD range test (p < 0.05).
Table 2. Results of the SIMPER analysis showing the average dissimilarity and the key discriminating species responsible for seasonal community.
Table 2. Results of the SIMPER analysis showing the average dissimilarity and the key discriminating species responsible for seasonal community.
Comparing Groups (1)Comparing Groups (2)Comparing Groups (3)
Monsoon and post-monsoon
26.98		Monsoon and winter
25.07		Post-monsoon and winter
28.33
Discriminator speciesDiscriminator speciesDiscriminator species
Neanthes sp.Siphonosoma cumanensePhascolosoma sp.
Siphonosoma cumanenseGlycera lancadivaeUrothoe lactea
Portunus sp. Neanthes sp.
Porcellio spinicornis Lycastonereis indica
Sphaeroma sp. Sphaeroma sp.
Pseudapocryptes elongatus
Comparing Groups (4)Comparing Groups (5)Comparing Groups (6)
Monsoon and pre-monsoon
Average dissimilarity = 22.46		Post-monsoon and pre-monsoon
Average dissimilarity = 29.67		Winter and pre-monsoon
Average dissimilarity = 21.78
Portunus sp.Phascolosoma sp.Lycastonereis indica
Neanthes sp.
Urothoe lactea
Pseudapocryptes elongatus		Dasybranchus sp.
Siphonosoma cumanense
Disclaimer/Publisher’s Note: The statements, opinions and data contained in all publications are solely those of the individual author(s) and contributor(s) and not of MDPI and/or the editor(s). MDPI and/or the editor(s) disclaim responsibility for any injury to people or property resulting from any ideas, methods, instructions or products referred to in the content.

Share and Cite

MDPI and ACS Style

Islam, M.S.; Zamal, H.; Alam, M.S.; Bappy, M.M.M.; Kamal, A.H.M.; Hossain, M.B.; Arai, T. Biodiversity and Seasonal Succession of Macrobenthos in Saltmarsh Habitat Adjacent to a Ship-Breaking Area. Diversity 2025, 17, 231. https://doi.org/10.3390/d17040231

AMA Style

Islam MS, Zamal H, Alam MS, Bappy MMM, Kamal AHM, Hossain MB, Arai T. Biodiversity and Seasonal Succession of Macrobenthos in Saltmarsh Habitat Adjacent to a Ship-Breaking Area. Diversity. 2025; 17(4):231. https://doi.org/10.3390/d17040231

Chicago/Turabian Style

Islam, M. Shafiqul, Hossain Zamal, Muhammad Shah Alam, Md. Maheen Mahmud Bappy, Abu Hena Mustafa Kamal, M. Belal Hossain, and Takaomi Arai. 2025. "Biodiversity and Seasonal Succession of Macrobenthos in Saltmarsh Habitat Adjacent to a Ship-Breaking Area" Diversity 17, no. 4: 231. https://doi.org/10.3390/d17040231

APA Style

Islam, M. S., Zamal, H., Alam, M. S., Bappy, M. M. M., Kamal, A. H. M., Hossain, M. B., & Arai, T. (2025). Biodiversity and Seasonal Succession of Macrobenthos in Saltmarsh Habitat Adjacent to a Ship-Breaking Area. Diversity, 17(4), 231. https://doi.org/10.3390/d17040231

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop