The Suva–Rewa–Tailevu corridor (Supplementary Figure S1), on the southeast coast of Fiji’s main island Viti Levu (approx. 18°S, 178°E), is home to more than 250,000 people (Wilson, 2012; Fiji Bureau of Statistics, 2017). The area combines dense urban settlement with intensive agriculture, insufficient waste management, and complex coastal processes increasing the susceptibility to MP accumulation (Drova et al., 2025). The adjacent Rewa River and Delta contain essential elasmobranch habitats (Brown et al., 2016; Glaus et al., 2019). Fishers from this region regularly bring their catch to the municipal market in Suva, particularly on Saturdays, which marks the main market day in Fiji (Glaus et al., 2024c). Twenty-two Fiji maskray specimens were purchased from a known local small-scale fisher between April 2024 and March 2025. The study objectives were explained to the fisher, and verbal consent for the use of specimens in University of the South Pacific (USP) research was obtained. Rays were reportedly caught opportunistically during nearshore gillnet fishing; no Fiji maskrays were caught specifically for this study. Captures occurred between Nausori and the Rewa Delta, but GPS positions and exact catch sites were not disclosed. Specimens were immediately transported to the USP Laucala Campus, and stored at −18 °C until processing.

Specimens were defrosted for approximately 20 h prior to measurements and dissection, rinsed with distilled water and dried. Specimens were weighed on an Ohaus Adventurer AX Precision Balance (model AX8201/E) to the nearest 0.01 g. Weight measurements included the head, trunk, pectoral, and pelvic fins, as tails had been cut off after capture to prevent injuries. Disc width in mm was measured on the dorsal side along the horizontal axis using a fish measuring board. Specimens were placed on a dissection tray, and a mid-ventral incision from the cloaca to the gill region was made with a sterile scalpel and forceps. To quantify MP contamination and compare presence between organs, the stomach and intestine were extracted. The liver was blotted dry with tissue paper and weighed to calculate the HSI. Liver color was recorded as a visual descriptor indicative for cell mutation (Agius, 1980; Neyrão et al., 2019), and classified as dark brown (DB) or light brown (LB). Stomach and intestine of each specimen were wrapped separately in aluminum foil, labeled, and stored at −18 °C until digestion. For digestion, stomach and intestine were processed separately. Each organ was placed into a labeled 600 mL glass beaker. A 10% Potassium Hydroxide, KOH, solution (volume ≥ 3× tissue volume) was added to dissolve soft tissue and food residues. Beakers were covered with aluminum foil and incubated at 60 °C for 48 h, with manual shaking after 24 h to ensure complete digestion (Amini-Birami et al., 2023). Digested material was then placed in a fume hood until further analysis.

Digested material from each specimen and organ was filtered through a sieve stack (500, 250, 125, and 63 µm) and allowed to settle for at least 3 min. To avoid MP cross-contamination, we followed procedures described in Pasalari et al. (2025); Trindade et al. (2023). Retained material was examined for MPs under an AmScope Stereo Microscope (SE306R-AZ-E1), using 2× magnification for 500 µm and 250 µm fractions and 4× for 125 µm and 63 µm fractions. For each observed MP particle, shape (fragment, fiber, film, foam, or microbead), sieve fraction, color, and the associated specimen ID were recorded in an Excel spreadsheet to ensure traceability. Microplastics were photographed using a Nikon Z8 with a 100mm f/2.8 Nikkor lens.

Sex was determined by the presence of claspers (males, M) or their absence (females, F), which are visible from early development along the inner margin of the pelvic fins (Allen and Robertson, 1994). Immature males have flexible claspers with little or no calcification, whereas mature males exhibit elongated, rigid, and fully calcified claspers (Stevens and McLoughlin, 1991). Hence, the maturity of male Fiji maskrays was determined by taking measurements of the clasper size post cloaca and clasper from the pelvic axis and determining its calcification (Campbell et al., 2021). In female specimens, maturity was assessed visually based on ovarian and uterine development (Pierce et al., 2009). The uterus is presented as a pair of thin, tubular extensions leading from the cloaca, while the ovaries were bilobed and located dorsally. We determined the following maturity categories: (1) Juvenile: little or no ovarian development and/or thin strap-like left uterus, (2) Subadult: differentiated and non vitellogenic follicles and/or partially expanded left uterus, (3) Mature: vitellogenic follicles of >1mm present in the ovary, left oviductal gland clearly differentiated from the ovary & uterus, and/or left uterus >10mm maximum width and trophonemata present. Juveniles and subadults were classified as immature.

The Excel data sheet (Davuke et al., 2025) was loaded into R Studio (R Core Team, 2025) with the readxl package (Wickham and Bryan, 2015). To clean the data, dplyr package was used (Wickham et al., 2014b). Additionally, tidyr allowed converting between long and wide data formats, and handled missing data values, which were earlier noted as “NA” (Wickham et al., 2014a). Microplastic contamination was expressed as mean ± standard deviation (SD). Specimens without MP were excluded from downstream analyses of MP characteristics (size, shape, color) distribution across organs (organs = stomach and intestine) or sexes. To test for differences in MP counts and MP characteristics among organs and between sexes, we fitted multifactor ANOVA models to log-transformed response variables. Model assumptions (normality and homoscedasticity) were evaluated using residual diagnostic plots. To complement the univariate analyses, we assessed multivariate differences in MP characteristic composition among organs using the R packages vegan (Oksanen et al., 2025) and cluster (Maechler et al., 2025).

To understand the physiological state and energy reserves, the HSI was calculated using the formula HSI=(Liver Weight (g)Body Weight (g))100. Since the measured weight excluded the tail (WT), we calculated two HSIs. First, HSI was computed using WT. Second, HSI was computed using an estimated total body weight. Total body weight (TW) was approximated by adding 2-5% percent to WT and averaging these four values to obtain the total-weight average (TWA) (e.g.

TW2%=(WT100)(100%+added tail weight of 2%). Differences in HSI between liver color groups were assessed with a One Way ANOVA. To analyze an association between liver color and sex, maturity, or size (DW), irrespective of MP contamination, we used a binomial generalized linear model (GLM) with the car package (Fox and Weisberg, 2019). Spearman rank correlations tested associations between HSI or DW and MP count. Size at maturity was summarized in sex-specific boxplots.

Figures were generated in R with qqplot2 (Wickham, 2016), Adobe Photoshop (Adobe Inc, 2023), and QGIS (QGIS Development Team, 2025).

Of 21 Fiji maskrays, MPs were detected in 15 individuals (~71.4%): in the stomach in three (~14.3%), the intestine only in one (~4.8%), and both organs in 11 (~52.4%). Six (~28.6%) had no MPs. Among individuals, the mean was 6.76 ± 7.80 particles per specimen. Particle counts did not differ between organs or sexes (p = 0.331, p = 0.222; Figure 1).

Microplastic sizes ranged from 63 to 500 µm in both stomach and intestine. Particles of 63 µm were most frequent, accounting for 34.8% of total MPs in the stomach and 22.0% in the intestine. Particles of 125 µm represented 26.1% and 34.0%, 250 µm particles 21.7% and 20.0%, and 500 µm particles 17.4% and 24.0% in stomach and intestine, respectively. No significant differences in particle size distribution were detected between organs or sexes (p = 0.379, p = 0.369).

Among the 15 contaminated Fiji maskrays, fragments were most abundant (n = 61), followed by films (n = 40) and fibers (n = 36). Shape distributions did not differ between organs or sexes for fibers, films, foams, fragments, or microbeads (p = 0.589, p = 0.717). In 12 contaminated individuals, white (n = 38) and silver (n = 33) dominated. Color distributions likewise did not differ between organs or sexes for black, blue, green, silver, transparent, or white (p = 0.483, p = 0.913). Overall, MP characteristics did not differ across organs (PERMANOVA, F = 0.911, R² = 0.016, p = 0.409; Figures 2, 3). Disc width was positively correlated with total MP count (Spearman ρ = 0.562, p = 0.008).

The HSI was calculated for 20 Fiji maskrays. Hepatosomatic index (WT and TWA) did not differ significantly between liver color groups (p = 0.052). Median values are 2.579 (DB) and 3.903 (LB) for WT, and 2.492 (DB) and 3.771 (LB) for TWA. However, no significant association between liver color and sex, maturity, DW or MP count was noted (GLM, p > 0.05). Although a weak to moderate negative correlation was found between MP presence and HSI (WT and TWA), this relationship was not statistically significant (p = 0.128, ρ = –0.352; Supplementary Table S1).

Size and sex were determined for 21 Fiji maskrays. One female (TV_Neotrygon_sp5) had undetermined maturity and was excluded, leaving 20 individuals for analysis (12 females, 60%; eight males, 40%). Among females, four were immature (33.3%; 293–361 mm DW; mean 327 ± 2.49 mm) and eight were mature (66.7%; 365–424 mm DW; mean 394 ± 2.55 mm). Among males, one was immature (12.5%; 311 mm DW) and seven were mature (87.5%; 369–395 mm DW; mean 381 ± 1.03 mm) (Figure 4). Males reached maturity at smaller maximum sizes than females.

Plastics are ubiquitously present across the lithosphere, hydrosphere and biosphere (Ziani et al., 2023), affecting marine ecosystems via habitat smothering, enhanced bioavailability, and toxin transfer along food chains (Jiang, 2018). This study reports the first data on MP contamination in the Fiji maskray from the Pacific island region. Overall, 71.43% of examined Fijian maskray individuals contained MPs, with contamination being somewhat higher in the stomach than in the intestine, albeit not significantly (p = 0.331; Figure 1). Microplastics ranged from 63 to 500 µm, with a mean of 6.76 ± 7.80 particles per specimen. Comparable contamination has been reported for other local marine taxa. For example, freshwater mussels (Batissa violacea) and shellfish (Anadara antiquata) from Viti Levu rivers had 0.9–5.9 MP particles per specimen (Barrientos et al., 2022; Powell et al., 2025). Among teleost fishes in Viti Levu, 67 - 74% of individuals contained MPs with mean loads of 1.8–17.0 particles per specimen, varying across locations (Ferreira et al., 2020; Drova et al., 2025).

Globally, demersal elasmobranchs average 4.0 ± 7.32 particles per specimen (Gong et al., 2024). Lower MP counts, averaging 2.4–3.8 particles per specimen, were reported for the Longnose stingray (Hypanus guttatus) and the Xingu freshwater stingray (Potamotrygon leopoldi) in Brazil. This likely reflects local exposure, with urban runoff and plastic waste retained in flooded forests, increasing fragmentation but limiting availability in main foraging channels (Pegado et al., 2021; Trindade et al., 2023). However, higher MP contamination (10.2 ± 7.4 MP particles/specimen) was detected in Haller’s Round stingrays (Urobatis halleri) from California, USA, an important small-scale fisheries habitat (Pinho et al., 2022). Nonetheless, compared to the Fiji maskray, stingrays from Brazil and California showed lower MP contamination rates across sample individuals, ranging from 30 - 60% (Pegado et al., 2021; Pinho et al., 2022; Trindade et al., 2023). Such differences may reflect lower local inputs, different sampling seasons or methods, or contrasts in habitat use and diet. Although the Fiji maskray shows higher MP counts than examined ray species in Brazil and slightly lower MP counts than rays in California, values fall within the range reported for benthic and demersal taxa around Viti Levu (Ferreira et al., 2020; Barrientos et al., 2022; Drova et al., 2025; Powell et al., 2025). This pattern points to local exposure pathways. The Suva–Rewa–Tailevu corridor has dense settlement and active small-scale fishery activities. Gillnets and other plastic gear that, when lost or discarded, degrade in situ thereby adding particles to nearshore habitats (Andrady, 2017; Godoy et al., 2019; Ferreira et al., 2020; Barrientos et al., 2022; Drova et al., 2025; Powell et al., 2025). Also, nearby agriculture and household runoff further add plastics and microfragments, especially along densely settled corridors, with likely amplified inputs from urban and peri-urban areas such as Nausori. Local hydrodynamics and retention in bays and reef-fringed lagoons can keep particles in contact with benthic feeders longer than in open coasts.

Understanding the origin of MPs is critical for reducing their presence and impacts on marine ecosystems. Microplastics are commonly categorized as pellets, fragments, films, or fibers (Guo and Wang, 2019). Microplastics found in the Fiji maskray were dominated by fragments, film, and fibers, with the majority being white or silver (Figures 2, 4). Teleost of Southeast Viti Levu showed similarities in shape dominance of fragments and fibers, and high SD of MP count between individuals (Ferreira et al., 2020). Southeast Viti Levu is strongly affected by wind, waves, and frequent flooding during cyclone season (Mangubhai et al., 2019). Insufficient waste management coupled with extreme weather conditions likely accelerates plastic breakdown (Varea et al., 2020; Drova et al., 2025), whereas plastics are washed through the continuum, eventually reaching the coastal area. Once plastics reach the coast, weathering can slowly break down larger particles into MPs. Also, strong UV radiation increases the degradation process of plastics (GESAMP, 2015). Additionally, discoloration of plastic particles occurs in advanced stages of degradation (Sutkar et al, 2023), possibly explaining the dominance of white and silver MPs in the Fiji maskray specimens.

In examined rays from other regions, fibers and blue colored MPs were predominant (Pegado et al., 2021; Pinho et al., 2022; Trindade et al., 2023). Fibers most likely originated from textile abrasion during washing (Mishra et al., 2024). Population density peaks in Suva, and comparably lower densities elsewhere within the Suva–Rewa–Tailevu corridor may translate into lower fiber inputs from domestic sources. By contrast, fragments and films are more likely to originate from discarded packaging and urban runoff (Burns and Boxall, 2018; Akdogan and Guven, 2019). Furthermore, MPs ingested by rays (Pinho et al., 2022; Pasalari et al., 2025) or demersal fish (Ferreira et al., 2020) are likely linked to MPs found in the sediments of the species habitat, its feeding strategy of how to obtain and select food sources, or MP contaminated prey. Fiji maskrays occur from the littoral zone to at least 23 m depth, inhabiting sandy bottoms, seagrass beds, muddy–sandy substrates, and coral reefs (Glaus et al., 2025). Microplastics that reach the ocean may sink and accumulate in benthic habitats (GESAMP, 2016). Given its nearshore habitat and likely benthic feeding, the Fiji maskray may be exposed to MP from urban runoff, littering, and textile fibers released via wastewater. We found no relevant sex-specific differences in MP uptake, suggesting that females and males either co-occur in the same habitats or that different habitats are affected to a comparable degree by MP pollution. The relatively high SD in particles per specimen may reflect this spatial heterogeneity or differing foraging histories. Due to the small sample size, variability is high, and a few extreme values can disproportionately affect the variance. Sampling was conducted year-round with the same fisher and methods within the same area, reducing procedural variation. However, as GPS positions were not disclosed, minor differences in capture location may have contributed to the observed variability. Nonetheless, it is plausible that Fiji maskrays are exposed to MPs throughout their life (Ferreira et al., 2020), corroborated by the positive monotonic relationship between size (DW) and MP (p = 0.008, ρ = 0.562). Contrastingly, Trindade et al. (2023) found no significant correlation between number of plastic particles and ray size (DW), possibly indicating that MP particles do not bioaccumulate.

Hepatosomatic index, being a morphometric index, is commonly used as a biological indicator, however its sensitivity requires careful interpretation (Martins et al., 2023). Although used to assess how environmental factors influence the health or physiological state of elasmobranchs, it can vary across species, seasons and environmental conditions (Reis and Figueira, 2020). Relative to values reported for rays sampled in Australia, Fiji maskray HSI appears lower than that of fiddler rays (Trygonorrhina fasciata; Reis and Figueira, 2020), but within the range reported for other members of the Neotrygon species complex (Pierce et al., 2009). Higher HSI values can be correlated with reproductive readiness (Pierce et al., 2009; Reis and Figueira, 2020). The weak to moderate negative correlation between MP presence and HSI, although not statistically significant, may indicate a subtle physiological response. Microplastic contamination can affect an individual’s molecular, biochemical, and cellular pathways (Avio et al., 2017), possibly leading to oxidative damage in gills and muscles, endocrine disruption, or cell mutation (Ašmonaitė et al., 2018; Varea et al., 2021). For example, in two species of catsharks (Scyliorhinus canicula & Galeus melastomus) from the Balearic Islands, with high MP contamination the detoxification process was activated and caused changes at cellular level (Torres et al., 2024). In addition, MP count had no significant effect on liver color, nor was liver color associated with sex, maturity, or body size. Given the relatively low HSI values and instances of liver darkening in Fiji maskrays, potential links between MP contamination and toxicological effects merit further investigation. Although total body weight was approximated using different tail-weight percentages to derive TWA, results were consistent across calculations.

Many batoids generally grow slowly, mature late, and have low fecundity compared to teleost fishes (Stevens et al., 2000; Pierce et al., 2009). Here, immature females measured 293–361 mm DW (n = 4), while mature females ranged from 365–424 mm (n = 9; Figure 3). We suggest that females reach sexual maturity at approximately 360–365 mm DW. The only immature male measured 311 mm DW, while mature males ranged between 369 and 395 mm (n = 7), pointing at a similar size at maturity, although more specimens are required to confirm this. Within the Neotrygon species complex, which has undergone several taxonomic revisions (Last et al., 2016), the southeast Queensland form previously assigned to N. kuhlii likely corresponds to other members of the complex, including the Coral Sea maskray (N. trigonoides) and the Australian bluespotted maskray (N. australiae). These species reach a larger maximum size of approximately 470 mm DW, with females maturing at around 314 mm and males at 294 mm (Pierce et al., 2009). Although the Fiji maskray reaches a smaller maximum size than other members of the Neotrygon species complex, it matures at a relatively larger proportion of its adult size. The warmer Fijian water could support faster somatic growth, where elevated temperatures may accelerate growth rates (Kingsolver, 2009) and size attainment but delay sexual maturation if more energy is initially allocated to growth. High prey availability in Fiji’s estuarine habitats may also support faster growth, with reproduction beginning only once sufficient energy reserves are reached. Future work examining vertebral band deposition (Mejía-Falla et al., 2014) would help determine growth rates and age at maturity in the Fiji maskray. Measuring sex pheromones in females could further clarify reproductive timing and temperature-related patterns (Elisio et al., 2019).

Fiji maskrays, like other co-occurring taxa, are exposed to locally derived MPs, with contamination increasing with body size yet not clearly reflected in hepatosomatic condition; future non-lethal, long-term field studies with larger sample sizes should target sublethal toxicological effects using biomarkers and repeated-measure condition indices and assess population-level consequences of chronic exposure. In parallel, systematic MP assessments and hotspot mapping (GESAMP, 2015), aligned with initiatives such as “Plastic Free Fiji” (United Nations, 2021), can help guide waste management and mitigation efforts to reduce plastic pollution pressure on South Pacific coastal ecosystems.