Parrotfishes were surveyed using two different methods: the Reef Visual Census program (See Smith et al 2011 and Brandt et al 2009 and https://grunt.sefsc.noaa.gov/rvc_analysis20/ for more information about this program) has been conducting a visual survey of reef fish species throughout the Florida Keys since 1978. The roving diver survey (see Adam et al 2015) was used in 2013 to collect data on parrotfishes only at several reefs in the Upper Florida Keys. Both datasets provide information on number of parrotfishes per unit area in selected locations in the Florida Keys. Parrotfish foraging parameters were also derived from behavioral observations of parrotfish feeding. See Adam et al 2015, 2018 for more details.

This activity uses REEF data to examine parrotfish population trends. Students practice data management and visualization, develop research questions and critically evaluate citizen science methods. Data interpretation, critical thinking, and communication skills are emphasized.

Background: Life is supported by the ecology and natural resources that exist on earth. Continents and oceans are the two main natural resources that host life and ecosystems around the world. 75% of the Earth's surface is covered by ocean waters that are rich in marine life. Although the oceans are vast, this does not mean that they are limitless. Population growth and development have led to an increase in the demand for marine resources. Increased demand and over-utilization of marine resources have led to strong pressures that have led to a decline in marine ecosystem services. Karimunjawa is famous for the natural beauty of its underwater coral reefs. Methods: This study employs a qualitative approach using literature and secondary data to examine the impact of parrotfish populations on coral reef sustainability. Findings: Based on current conditions, excessive catching of parrotfish has a negative impact on the sustainability of coral reefs in Karimunjawa National Park. It is necessary for local communities to understand the importance of the role of parrot fish for the sustainability of marine ecosystems. Parrotfish spend 90% of their time eating algae attached to coral reefs. Damage to the coral reef ecosystem causes coastal erosion in Karimunjawa National Park. Therefore, the role of the community in managing parrotfish resources is very necessary so as not to threaten the population for the sustainability of the marine ecosystem. Conclusion: The results of this research illustrate the role of humans, namely the community and tourists who come to Karimunjawa to carry out activities to preserve damaged coral reefs and create new coral reef areas. Novelty/Originality of this article: There are also government policies that must be considered and implemented properly for the sustainability of coral reef ecosystems and the conservation of parrotfish in Karimunjawa.

parrotfishes.csv metadata:

Site - Fringing Reef Sites: AC, Angel City; AQ, Aquarius; BB, Bachelor's Beach; IV, Invisibles; TL, The Lake.

NamePhase - Common name and ontogenetic phase (initial and terminal phase; IP and TP, respectively) of the parrotfishes observed.

CommonName - Common names of parrotfishes observed.

ScientificName - Scientific names of parrotfishes observed.

Transect - Transect number (e.g., T1 is transect 1).

Bin - Parrotfishes were binned by forklength (cm) and these values indicate size class that fishes were binned into (e.g., B6.10 is for fishes 6-10cm forklength).

AvgLength - The average forklength (cm) for each bin.

Density - Counts of parrotfishes per 100-m2 band transect (25-m x 4-m) for a given species/phase/bin.

Biomass - Biomass (g 100 m-2) of each row calculated using AvgLength, Density, and species-specific published length-weight ratios (Bohnsack and Harper 1988).

benthic-cover.csv metadata:

Site - Fringin...

To determine the patterns and thresholds of tissue regeneration in Orbicella annularis coral colonies from parrotfish predation, we monitored tissue regeneration of fresh parrotfish bite scars on O. annularis colonies over time across two Caribbean islands, St. Croix and Bonaire. We monitored colonies on St. Croix from June to July 2018 for up to 28 days on Bonaire from June to August 2019 for up to 64 days. This file includes the four datasets used in our study entitled 'Impacts of parrotfish predation on a major reef-building coral: quantifying healing rates and thresholds of coral recovery' (https://doi.org/10.1007/s00338-020-01977-9). For a detailed description of methods, please refer to this publication. Dataset overview: 1) 'A1_data_overview.csv', a file that describes each variable within each of the subsequent datasets. 2) OANN_scar_healing_after_up_to_28_days.csv, the total observed tissue regeneration of parrotfish bite scars on Orbicella annularis colonies on St. Croix and Bonaire between the initial monitoring date and after 21-28 days of monitoring. 3) OANN_scar_healing_after_up_to_64_days.csv, the total observed tissue regeneration of parrotfish bite scars on Orbicella annularis colonies on Bonaire between the initial monitoring data and after 55-64 days of monitoring. 4) OANN_scar_healing_time_series.csv, time series observations of tissue regeneration of parrotfish bite scars on Orbicella annularis colonies on St. Croix and Bonaire between each 2-7 day monitoring interval over the course of the study. There are multiple, successive observations of tissue regeneration for each scars on each monitoring day. 5) OANN_scar_standing_stock.csv, the distribution of haphazardly surveyed parrotfish predation scars on St. Croix and Bonaire at a point in time observed within 30m x 1m belt transects conducted across a range of depths up to 18m. This dataset includes the total abundance of scars per colony, the number of fresh bite scars, and the estimated minimum, median, and maximum observed scar per colony and colony size measurements for all Orbicella annularis colonies with parrotfish predation scars present within transects. Methods overview: We conducted this at four sites on St. Croix from June to July of 2018 and four sites on Bonaire from June to August of 2019. At each site, we opportunistically tagged O. annularis colonies with recent parrotfish bite scars. For each colony, we recorded the colony surface area, depth in the water column, and the abundance of recent parrotfish bite scars. For each scar on the colony, we took a close up photograph of the scar with a size reference. We returned to photograph scars every 2 to 7 days, with more frequent monitoring at the start of the study. On St. Croix, we monitored scars for 21- 28 days or until the scars fully healed (i.e., a soft tissue layer had completely enclosed the scar area). Research on tissue regeneration in O. annularis suggests that the majority of scar tissue regeneration occurs within the first few weeks after scars are inflicted, though scars may continue to heal for up to almost two months (Meesters et al. 1994, 1997). Therefore, on Bonaire, we monitored scars for 55- 64 days or until scars fully healed. We used Image J 1.46r to trace and measure the surface area of each scar on a given monitoring day and used these measurements to calculate change in scar area over time. References: Meesters EH, Noordeloos M, Bak RPM (1994) Damage and regeneration: Links to growth in the reef-building coral Montastraea annularis. Mar Ecol Prog Ser 112:119-128 Meesters EH, Pauchli W, Bak RPM (1997) Predicting regeneration of physical damage on a reef-building coral by regeneration capacity and lesion shape. Mar Ecol Prog Ser 146:91-99

Additional file 1: Table S1. Results of the permutational ANOVA on the bacterial assemblages according to the sample type (control, predated coral and fish mouth) assessed at Ti and Tf for the mesocosm experiment. Table S2. Results of pair-wise tests on the effect of the sample type on the bacterial assemblages for the mesocosm experiment at Ti and Tf. Table S3. Average relative abundance of the families present in the fish mouths for the mesocosm experiment. Table S4. Average relative abundance of the families present in mechanically wounded corals at Ti for the mesocosm experiment. Table S5. Average relative abundance of the families present in mechanically wounded corals at Tf. Table S6. Average relative abundance of the families present in the predated corals at Ti for the mesocosm experiment. Table S7. Average relative abundance of families present in predated corals at Tf. Table S8. Results of the permutational ANOVA on the bacterial assemblages according to the sample type assessed for field experiment including or not water samples. Table S9. Results of pair-wise tests on the effect of the sample type on the bacterial assemblages for the field experiment. Table S10. Average relative abundance of the families present in the fish mouths for the field experiment. Table S11. Average relative abundance of the families present in naturally unbitten corals in the field. Table S12. Average relative abundance of families present in bitten corals for the field experiment. Table S13. Results of ANOVA and non-parametric tests of the effect of the sample type on alpha diversity metrics (Observed Richness and Shannon-Wiener Index) for the mesocosm experiment at Ti and Tf. Table S14. Results of posthoc tests assessing the effect of the sample type on alpha diversity metrics (Observed Richness and Shannon-Wiener index) for the mesocosm experiment at Ti and Tf. Table S15. Results of ANOVA and non-parametric tests on the effect of the type of sample on alpha diversity metrics (Observed Richness and Shannon-Wiener index) for the field experiment. Table S16. Results of posthoc tests on the effect of the sample type on alpha diversity metrics (Observed Richness and Shannon-Wiener index) for the field experiment. Table S17. Results from differential abundance analyses (DESeq2) on the effect of the sample type at Ti for the mesocosm experiment. Table S18. Average relative abundance of taxa present in greater differential abundance in predated corals compared to mechanically wounded corals for the mesocosm experiment at Ti and Tf. Table S19. Results from differential abundance analyses (DESeq2) on the effect of the sample type at Tf for the mesocosm experiment. Table S20. Differential abundance analysis for the field experiment according to the sampletype. Table S21. Average relative abundance of taxa present in greater differential abundance in naturally bitten corals compared to controls for the field experiment. Table S22. Results of Permutation test for homogeneity of multivariate dispersions (betadisper) on the effect of the sample type in the field survey. Table S23. Results of Permutation test for homogeneity of multivariate dispersion (betadisper) on the effect of the sample type in the field survey. Table S24. filtered unprocessed sOTU table for the mesocosm experiment. Table S25. Taxa table for the negative control of the mesocosm experiment. Table S26. filtered unprocessed sOTU table for the field survey. Table S27. Taxa table for the negative control in the field survey.

Data associated with the publication 'Ecological drivers of parrotfish coral predation vary across spatial scales', comparing parrotfish coral predation intensity as it relates to parrotfish density/biomass, coral cover, and other ecological variables from the scale of individual coral colonies to reefs spanning four regions of the Greater Caribbean. This dataset includes several datasets: 1) regional_coral_scar_data.csv: Surveys of coral colonies (with and without parrotfish predation scars) across all regions. 2) processed_coral_scar_data_colony_level.csv: Processed data from the file above filtered to only include coral taxa commonly predated by parrotfishes (determined as coral taxa for which at least 3 colonies across the entire dataset had 3 recent parrotfish predation scars). This includes the calculated coral colony surface area and the estimated total/sum recent scar area per coral colony. 3) regional_fish_data.csv: Parrotfish abundance and size for individuals greater than or equal to 15 cm fork length. This data includes estimated fish weight and related length-weight conversion values used to calculate these values. 4) site_coordinates.csv: Metadata of the latitude and longitude of all study sites.

To better understand the functional roles of parrotfishes on Caribbean coral reefs we documented abundance, habitat preferences, and diets of nine species of parrotfishes (Scarus coelestinus, Scarus coeruleus, Scarus guacamaia, Scarus taeniopterus, Scarus vetula, Sparisoma aurofrenatum, Sparisoma chrysopterum, Sparisoma rubripinne, Sparisoma viride) on three high-relief spur-and-groove reefs (Molasses, Carysfort, and Elbow) offshore of Key Largo in the Florida Keys National Marine Sanctuary. On each reef, we conducted fish surveys, behavioral observations, and benthic surveys in three habitat types: high-relief spur and groove (depth 2 - 6 m), low-relief carbonate platform/hardbottom (depth 4 - 12 m), and carbonate boulder/rubble fields (depth 4 - 9 m). In addition, fish surveys were also conducted on a fourth high-relief spur-and-groove reef (French). We estimated parrotfish abundance in each of the three habitat types in order to assess the relative abundance and biomass of different species and to quantify differences in habitat selection. To estimate parrotfish density, we conducted 20 to 30 minute timed swims while towing a GPS receiver on a float on the surface to calculate the amount of area sampled. During a swim the observer would swim parallel with the habitat type being sampled and count and estimate the size to the nearest cm of all parrotfishes greater than or equal to 15 cm in length that were encountered in a 5 m wide swath. To quantify parrotfish behavior, approximately six individuals of each species were observed at each site for 20 min each. Foraging behavior was recorded by a SCUBA diver while towing a GPS receiver (Garmin GPS 72) attached to a surface float, which obtained position fixes of the focal fish at 15 s intervals. Fish were followed from a close distance (~ 2 m when possible), and food items were identified to the lowest taxonomic level possible, with macroalgae and coral usually identified to genus or species. Many bites involved scraping or excavating substrate colonized by a multi-species assemblage of filamentous “turf†algae and crustose coralline algae (CCA). Thus, multiple species of filamentous algae, endolithic algae, and CCA could be harvested in a single bite, and it was impossible to determine the specific species of algae targeted. We also recorded the type of substrate targeted during each foraging bout, categorizing each substrate as one of the following: (1) dead coral, (2) coral pavement, (3) boulder, (4) rubble, or (5) ledge. Dead coral included both convex and concave surfaces on the vertical and horizontal planes of three dimensional coral skeletons (primarily dead Acropora palmata) that were attached to reef substrate. Coral pavement was carbonate reef with little topographic complexity (i.e., flat limestone pavement). Boulder was large remnants of dead mounding corals not clearly attached to the bottom and often partially buried in sand. Coral rubble consisted of small dead coral fragments (generally < 10 cm in any dimension) that could be moved with minimal force. Ledges consisted entirely of the undercut sides of large spurs in the high-relief spur and groove habitat. In order to quantify the relative abundance of different food types, we estimated the percent cover of algae, coral, and other sessile invertebrates on each of the five substrates commonly targeted by parrotfishes (dead coral, coral pavement, boulder, rubble, or ledge) in 0.5 m x 0.5 m photoquadrats. We photographed a total of 8 haphazardly selected quadrats dispersed throughout the study site for each substrate type at each of the three sites (N = 24 quadrats per substrate type, N = 120 quadrats total). Each photoquadrat was divided into sixteen 12 cm x 12 cm sections which were individually photographed, and percent cover was estimated from 9 stratified random points per section (N = 144 point per quadrat).

in situ visual surveys of reproductive behavior, spawning and courtship events

Animals often occupy home ranges where they conduct daily activities. In many parrotfishes, large terminal phase (TP) males defend their diurnal (i.e., daytime) home ranges as intraspecific territories occupied by harems of initial phase (IP) females. However, we know relatively little about the exclusivity and spatial stability of these territories. We investigated diurnal home range behavior in several TPs and IPs of five common Caribbean parrotfish species on the fringing coral reefs of Bonaire, Caribbean Netherlands. We computed parrotfish home ranges to investigate differences in space use and then quantified spatial overlap of home ranges between spatially co-occurring TPs to investigate exclusivity. We also quantified spatial overlap of home ranges estimated from repeat tracks of a few TPs to investigate their spatial stability. We then discussed these results in the context of parrotfish social behavior. Home range sizes differed significantly among species. Spatial overlap between home ranges was lower for intraspecific than interspecific pairs of TPs. Focal TPs frequently engaged in agonistic interactions with intraspecific parrotfish and interacted longest with intraspecific TP parrotfish. This behavior suggests that exclusionary agonistic interactions may contribute to the observed patterns of low spatial overlap between home ranges. Spatial overlap of home ranges estimated from repeated tracks of several TPs of three study species was high, suggesting that home ranges were spatially stable for at least one month. Taken together, our results suggest that daytime parrotfish space use is constrained within fixed intraspecific territories in which territory holders have nearly exclusive access to resources. Grazing by parrotfishes maintains benthic reef substrates in early successional states that are conducive to coral larval settlement and recruitment. Behavioral constraints on parrotfish space use may drive spatial heterogeneity in grazing pressure and affect local patterns of benthic community assembly. A thorough understanding of the spatial ecology of parrotfishes is, therefore, necessary to elucidate their functional roles on coral reefs. Methods Study species and sites We conducted our research on Scarus iseri, Scarus taeniopterus, Scarus vetula, Sparisoma aurofrenatum, and Sparisoma viride at five fringing coral reefs along the leeward coast of Bonaire during January (Winter) and May-July (Summer) 2019: Angel City (12.10305º, -68.28852º), Aquarius (12.09824º, -68.28624º), Bachelor’s Beach (12.12605º, -68.28819º), Invisibles (12.07805º, -68.28175º), and The Lake (12.10618º, -68.29079º). The fringing coral reefs of Bonaire, Caribbean Netherlands have remained resilient despite multiple disturbances, and boast higher coral cover than most Caribbean coral reefs (Perry et al. 2013, Steneck et al. 2019). The abundance and biomass of different fish groups, including parrotfishes, is also much higher on Bonaire’s coral reefs compared to more heavily fished reefs in the Eastern Caribbean (Hawkins & Roberts 2003, 2004, Steneck et al. 2019). The benthic composition across our study sites was similar, with relatively high coral cover (~20%) and low macroalgal cover (< 3%; Manning & McCoy 2022). Additionally, our five focal parrotfish species comprised more than 96% of the parrotfish biomass at our study sites (Manning & McCoy 2022). Parrotfish tracking We conducted concurrent GPS tracking and behavioral observations of TP and IP parrotfishes between 1000–1600 hrs, peak foraging times for parrotfishes (Bruggemann et al. 1994b a). We identified focal parrotfish (TP or IP) haphazardly at ~10 m depth on SCUBA at each site. Each fish was then allowed to acclimate to diver presence for approximately 1–2 mins, during which time we visually estimated standard length (to the nearest cm) by measuring the distance between reference objects passed by the fish using a collapsible meter-stick. We then estimated body mass (g) from standard length using published length-weight relationships (Bohnsack & Harper 1988; Appendix: Table A1). We followed focal fish from ~2 m, and recorded their behavior in high resolution (4K) using a GoPro Hero 4 Silver (GoPro, Inc) attached to a ‘selfie-stick’. Focal parrotfishes were tracked at the surface by a snorkeler carrying a handheld GPS receiver (Garmin GPSMap 78sc, United States of America) for 13.56 ± 0.19 mins (mean ± SE, n = 215 total tracks). The GPS receiver was set to record data as often as possible, resulting in a mean (± SE) relocation interval of 12.32 ± 0.21 s (mean ± SE, n = 215 total tracks). We ensured that we did not track the same individuals unintentionally by progressively moving north along the reef, using reference structures, until we identified another unique individual to observe. A few times, we unintentionally conducted repeat tracks of previously tracked individuals (on the same day or within a few days; confirmed as described below). In such cases, unintentional repeat tracks were excluded from our analyses. Because our interest was in the home range behavior of territorial fishes, we excluded non-territorial, transient TP fishes from our analyses. Transient, non-territorial TPs were not site attached and were frequently chased along the reef by territory holders. We preliminarily tracked several territorial TP (hereafter, just TP) Sp. viride at two sites in Winter 2019. Then, during Summer 2019, we tracked several TP Sc. taeniopterus, Sc. vetula, and Sp. viride at all five sites, and TP Sc. iseri and Sp. aurofrenatum at two sites. To investigate differences in space use among ontogenetic phases, we also tracked IP Sc. taeniopterus, Sc. vetula, and Sp. viride at two sites during Summer 2019. Finally, to quantify short-term spatial stability of parrotfish home ranges (described below), we conducted planned repeat tracks of several TP Sc. taeniopterus, Sc. vetula, and Sp. viride at two sites during Summer 2019. Repeat tracks were obtained by tracking TPs along the same portions of the reef where they had been tracked ~1 month prior. Individual parrotfish are identifiable by unique color patterns and markings on their bodies (Dubin 1981, van Rooij et al. 1996). We compared color patterns and markings of each fish using stills taken from our video recorded behavioral observations to confirm that initial and repeat tracks were of the same fish and not different fish occupying the same areas (Figures A1-A3). We also obtained unplanned, repeat tracks of 4 TP Sp. viride at Angel City and Bachelor’s Beach (n = 2 per site) during Summer 2019 that were initially tracked in January 2019. Home ranges of the 4 fish were in the same locations in both tracking periods, and visual observation of color patterns and markings from video stills confirmed that they were the same fish. A full breakdown of our sampling effort is reported in the Appendix (Table A2). Home range estimationVisual analyses of stationarity confirmed that our GPS tracks were sufficiently long to capture home range behavior (Figure A4; Benhamou 2014). We used movement-based kernel density estimation (MKDE) to estimate utilization distributions from our tracks of individual parrotfishes (sensu Benhamou 2011), and define home range and core use areas as the areas underneath the 95% and 50% cumulative isopleths of each utilization distribution, respectively. Though we used MKDE estimates of home ranges for analyses of space use in our study, we also present home range sizes estimated using traditional location-based kernel density estimation (ad hoc bandwidth selection) and minimum convex polygons to facilitate comparisons of home range area with other studies (Table A3). All home ranges and core use areas were computed in the adehabitatHR package in R (Calenge 2006, R Core Team 2020).Home range exclusivity and stabilityTo investigate the exclusivity of parrotfish HRs, we quantified spatial overlap between HRs of spatially co-occurring TP parrotfishes tracked during Summer 2019. This measure of spatial overlap estimates shared space use between neighboring fish that are sharing at least some space on the reef. We used only HRs estimated from the first GPS track of TPs for which we had replicate GPS tracks. Spatial overlap was estimated using Bhattacharyya’s Affinity (BA), a function of the product of two utilization distributions that ranges from 0 (no overlap) to 1 (perfect overlap) and is a strong metric of joint space use between animals, particularly when comparing utilization distributions estimated for the same animal at different times (Fieberg & Kochanny 2005). As such, we also used BA to quantify the spatial overlap of HRs estimated from repeat tracks of TP Sc. taeniopterus, Sc. vetula, and Sp. viride to determine the spatial stability of those HRs. To distinguish spatial overlap between different spatially co-occurring individuals and spatial overlap of home ranges estimated from repeat tracks of the same individuals, we use the terms spatial overlap and temporal overlap, respectively. Spatial and temporal overlaps of MKDE home ranges were computed in the adehabitatHR package in R (Calenge 2006). Occupancy changeDuring our attempt to repeatedly track parrotfishes at Aquarius, we observed an occupancy change in a TP Sc. vetula home range. We analyzed this occupancy change as a separate case study (Figure A5). To investigate how a change in occupancy affected space use, we quantified spatial overlap between the home range of the new occupant and the home range of the old occupant. We also quantified spatial overlap between the home range of the new occupant and the home ranges of spatially co-occurring intraspecific and interspecific fishes from the initial tracking (Table A4).Social behavior We quantified the social behavior of the TP parrotfishes tracked in Summer 2019 (n = 128) by analyzing the video recordings of the initial tracks for each fish (when repeat

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Species-specific projected total habitat suitability index (HSI) and HSI's change or 'anomaly' under different carbon dioxide emission levels, including (A) total HSI for the 1970 to 2000 period; and changes in HSI under scenarios of (B) ~400 ppm and (C) ~565 ppm atmospheric carbon dioxide concentration in the high resolution Earth system model (GFDL CM2.6).

Subscribers can find out export and import data of 23 countries by HS code or product’s name. This demo is helpful for market analysis.

This dataset provides information about the number of properties, residents, and average property values for Parrotfish Court cross streets in Waldorf, MD.

This dataset contains parrotfish bite observations for the study plots at Pickles Reef, Florida Keys National Marine Sanctuary from 2009-2013. Published in Nature Communications (2016) doi:10.1038/ncomms11833, Supplementary Data 2c.

Natural history of the study site:
This experiment was conducted in the area of Pickles Reef (24.99430, -80.40650), located east of Key Largo, Florida in the United States. The Florida Keys reef tract consists of a large bank reef system located approximately 8 km offshore of the Florida Keys, USA, and paralleling the island chain. Our study reef is a 5-6 m deep spur and groove reef system within this reef tract. The reefs of the Florida Keys have robust herbivorous fish populations and are relatively oligotrophic. Coral cover on most reefs in the Florida Keys, including our site, is 5-10%, while macroalgal cover averages ~15%, but ranges from 0-70% depending on location and season. Parrotfishes (Scaridae) and surgeonfishes (Acanthuridae) are the dominant herbivores on these reefs as fishing for them was banned in 1981. The other important herbivore on Caribbean reefs, the urchin Diadema antillarum, remains at low densities across the Florida Keys following the mass mortality event in 1982-3.

Related Reference:
Zaneveld, J.R., D.E. Burkepile, A.A. Shantz, C. Pritchard, R. McMinds, J. Payet, R. Welsh, A.M.S. Correa, N.P. Lemoine, S. Rosales, C.E. Fuchs, and R. Vega Thurber (2016) Overfishing, nutrient pollution, and temperature interact to disrupt coral reefs down to microbial scales. Nature Communications 7:11833 doi:10.1038/ncomms11833 Supplementary Information

This dataset provides information about the number of properties, residents, and average property values for Parrotfish Street cross streets in Venice, FL.

Data from behavioural experiments undertaken at The Cape Eleuthera Institute in the summer of 2024 to examine predator-prey dynamics between invasive lionfish and native Caribbean parrotfish under different scenarios.

No description is available. Visit https://dataone.org/datasets/sha256%3Afc1b86b46b2706a33845ab1022838cf628317e4d155b719749690c812a108d2a for complete metadata about this dataset.

Stoplight parrotfish and queen parrotfish eye lens core validation samples.