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<journal-meta>
<journal-id journal-id-type="publisher-id">Front. Remote Sens.</journal-id>
<journal-title>Frontiers in Remote Sensing</journal-title>
<abbrev-journal-title abbrev-type="pubmed">Front. Remote Sens.</abbrev-journal-title>
<issn pub-type="epub">2673-6187</issn>
<publisher>
<publisher-name>Frontiers Media S.A.</publisher-name>
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<article-meta>
<article-id pub-id-type="publisher-id">1338586</article-id>
<article-id pub-id-type="doi">10.3389/frsen.2024.1338586</article-id>
<article-categories>
<subj-group subj-group-type="heading">
<subject>Remote Sensing</subject>
<subj-group>
<subject>Original Research</subject>
</subj-group>
</subj-group>
</article-categories>
<title-group>
<article-title>Unidentified fish sounds as indicators of coral reef health and comparison to other acoustic methods</article-title>
<alt-title alt-title-type="left-running-head">Jarriel et al.</alt-title>
<alt-title alt-title-type="right-running-head">
<ext-link ext-link-type="uri" xlink:href="https://doi.org/10.3389/frsen.2024.1338586">10.3389/frsen.2024.1338586</ext-link>
</alt-title>
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<contrib-group>
<contrib contrib-type="author" corresp="yes">
<name>
<surname>Jarriel</surname>
<given-names>Sierra D.</given-names>
</name>
<xref ref-type="aff" rid="aff1">
<sup>1</sup>
</xref>
<xref ref-type="corresp" rid="c001">&#x2a;</xref>
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<contrib contrib-type="author">
<name>
<surname>Formel</surname>
<given-names>Nathan</given-names>
</name>
<xref ref-type="aff" rid="aff1">
<sup>1</sup>
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<contrib contrib-type="author">
<name>
<surname>Ferguson</surname>
<given-names>Sophie R.</given-names>
</name>
<xref ref-type="aff" rid="aff1">
<sup>1</sup>
</xref>
<xref ref-type="aff" rid="aff2">
<sup>2</sup>
</xref>
<xref ref-type="fn" rid="fn1">
<sup>&#x2020;</sup>
</xref>
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<contrib contrib-type="author">
<name>
<surname>Jensen</surname>
<given-names>Frants H.</given-names>
</name>
<xref ref-type="aff" rid="aff1">
<sup>1</sup>
</xref>
<xref ref-type="aff" rid="aff3">
<sup>3</sup>
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<contrib contrib-type="author">
<name>
<surname>Apprill</surname>
<given-names>Amy</given-names>
</name>
<xref ref-type="aff" rid="aff4">
<sup>4</sup>
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<contrib contrib-type="author" corresp="yes">
<name>
<surname>Mooney</surname>
<given-names>T. Aran</given-names>
</name>
<xref ref-type="aff" rid="aff1">
<sup>1</sup>
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<aff id="aff1">
<sup>1</sup>
<institution>Biology Department</institution>, <institution>Woods Hole Oceanographic Institution</institution>, <addr-line>Woods Hole</addr-line>, <addr-line>MA</addr-line>, <country>United States</country>
</aff>
<aff id="aff2">
<sup>2</sup>
<institution>Marine Biological Laboratory</institution>, <addr-line>Woods Hole</addr-line>, <addr-line>MA</addr-line>, <country>United States</country>
</aff>
<aff id="aff3">
<sup>3</sup>
<institution>Department of Ecoscience</institution>, <institution>Aarhus University</institution>, <addr-line>Aarhus</addr-line>, <country>Denmark</country>
</aff>
<aff id="aff4">
<sup>4</sup>
<institution>Marine Chemistry and Geochemistry Department</institution>, <institution>Woods Hole Oceanographic Institution</institution>, <addr-line>Woods Hole</addr-line>, <addr-line>MA</addr-line>, <country>United States</country>
</aff>
<author-notes>
<fn fn-type="edited-by">
<p>
<bold>Edited by:</bold> <ext-link ext-link-type="uri" xlink:href="https://loop.frontiersin.org/people/954397/overview">DelWayne Roger Bohnenstiehl</ext-link>, North Carolina State University, United States</p>
</fn>
<fn fn-type="edited-by">
<p>
<bold>Reviewed by:</bold> <ext-link ext-link-type="uri" xlink:href="https://loop.frontiersin.org/people/1101439/overview">Timothy J. Rowell</ext-link>, National Oceanic and Atmospheric Administration (NOAA), United States</p>
<p>
<ext-link ext-link-type="uri" xlink:href="https://loop.frontiersin.org/people/1209112/overview">Carrie Wall</ext-link>, University of Colorado Boulder, United States</p>
</fn>
<corresp id="c001">&#x2a;Correspondence: Sierra D. Jarriel, <email>sierra.jarriel@whoi.edu</email>; T. Aran Mooney, <email>amooney@whoi.edu</email>
</corresp>
<fn fn-type="other" id="fn1">
<label>
<sup>&#x2020;</sup>
</label>
<p>
<bold>Present address:</bold> Sophie R. Ferguson, Integrated Statistics, under contract to the Northeast Fisheries Science Center, National Marine Fisheries Service, National Oceanic and Atmospheric Administration, MA, USA</p>
</fn>
</author-notes>
<pub-date pub-type="epub">
<day>01</day>
<month>03</month>
<year>2024</year>
</pub-date>
<pub-date pub-type="collection">
<year>2024</year>
</pub-date>
<volume>5</volume>
<elocation-id>1338586</elocation-id>
<history>
<date date-type="received">
<day>14</day>
<month>11</month>
<year>2023</year>
</date>
<date date-type="accepted">
<day>05</day>
<month>02</month>
<year>2024</year>
</date>
</history>
<permissions>
<copyright-statement>Copyright &#xa9; 2024 Jarriel, Formel, Ferguson, Jensen, Apprill and Mooney.</copyright-statement>
<copyright-year>2024</copyright-year>
<copyright-holder>Jarriel, Formel, Ferguson, Jensen, Apprill and Mooney</copyright-holder>
<license xlink:href="http://creativecommons.org/licenses/by/4.0/">
<p>This is an open-access article distributed under the terms of the Creative Commons Attribution License (CC BY). The use, distribution or reproduction in other forums is permitted, provided the original author(s) and the copyright owner(s) are credited and that the original publication in this journal is cited, in accordance with accepted academic practice. No use, distribution or reproduction is permitted which does not comply with these terms.</p>
</license>
</permissions>
<abstract>
<p>The global decline of coral reefs is a major contributor to the global biodiversity crisis and requires improved monitoring at these critically important habitats. Non-invasive passive acoustic assessments may address this need, leveraging the rich variety and spatiotemporal variability of biological sounds present in coral reef environments and offering near-continuous temporal coverage. Despite this, acoustic metrics that reliably represent coral reef health are still debated, and ground-truthing of methods is limited. Here we investigated how the prevalence of low frequency biotic sounds (without species information) relates to coral reef health, providing a foundation from which one can compare assessment methods. We first quantified call rates of these low frequency sounds for three reefs exhibiting different community assemblages around St. John, U.S. Virgin Islands, by manually annotating presumed fish noises for 1&#xa0;min every 30&#xa0;min across 8&#xa0;days for each site. Annotated days were selected at key points across lunar cycles. These call rates were then compared with traditional visual surveys, and several acoustic methods and indices commonly used in underwater soundscape research. We found that, overall, manually detected fish call rates successfully differentiated between the three reefs, capturing variation in crepuscular activity levels&#x2013;a pattern consistent with previous work that highlights the importance of diel choruses. Moreover, fish vocal rates were predictors of hard coral cover, fish abundance, and fish species richness, while most acoustic indices failed to parse out fine distinctions among the three sites. Some, such as the Acoustic Complexity Index, failed to reveal any expected differences between sites or times of day, while the Bioacoustic Index could only identify the most acoustically active reef, otherwise having weak correlations to visual metrics. Of the indices tested, root-mean-squared sound pressure level and Acoustic Entropy, both calculated in the low frequency fish band (50&#x2013;1,200&#xa0;Hz), showed the strongest association with visual health measures. These findings present an important step toward using soundscape cues for reef health assessments. The limited generalizability of acoustic indices across different locations emphasizes the need for caution in their application. Therefore, it is crucial to improve methods utilizing fish sounds, such as automatic fish call detectors that are able to generalize well to new soundscapes.</p>
</abstract>
<kwd-group>
<kwd>fish calls</kwd>
<kwd>soundscapes</kwd>
<kwd>acoustic indices</kwd>
<kwd>unknown sounds</kwd>
<kwd>biodiversity</kwd>
</kwd-group>
<contract-sponsor id="cn001">Richard Lounsbery Foundation<named-content content-type="fundref-id">10.13039/100017651</named-content>
</contract-sponsor>
<custom-meta-wrap>
<custom-meta>
<meta-name>section-at-acceptance</meta-name>
<meta-value>Acoustic Remote Sensing</meta-value>
</custom-meta>
</custom-meta-wrap>
</article-meta>
</front>
<body>
<sec sec-type="intro" id="s1">
<title>1 Introduction</title>
<p>As one of Earth&#x2019;s most biodiverse ecosystems, coral reefs are hotspots of biological activity (<xref ref-type="bibr" rid="B70">Reaka-Kudla, 1997</xref>). They provide valuable resources to humans, including vital fisheries (<xref ref-type="bibr" rid="B44">Newton et al., 2007</xref>), tourism (<xref ref-type="bibr" rid="B57">Spalding et al., 2017</xref>), and coastal protection (<xref ref-type="bibr" rid="B64">van Zanten et al., 2014</xref>), making them a source of livelihood for many lower-latitude nations (<xref ref-type="bibr" rid="B5">Birkeland, 1997</xref>; <xref ref-type="bibr" rid="B10">Cinner, 2014</xref>). However, in recent decades, reef-building corals and associated biodiversity have experienced a dramatic and unprecedented decline, reducing their contributions to these communities by half (<xref ref-type="bibr" rid="B13">Eddy et al., 2021</xref>). The need to study and monitor reef health using non-invasive and scalable tools has led to the development of diverse monitoring techniques (<xref ref-type="bibr" rid="B2">Apprill et al., 2023</xref>), such as eDNA (<xref ref-type="bibr" rid="B67">West et al., 2020</xref>), remote-sensing (<xref ref-type="bibr" rid="B40">Mumby et al., 2004</xref>; <xref ref-type="bibr" rid="B30">Liu et al., 2005</xref>), visual imaging and surveys (<xref ref-type="bibr" rid="B33">Mallet and Pelletier, 2014</xref>), and passive acoustics (<xref ref-type="bibr" rid="B23">Kaplan et al., 2015</xref>; <xref ref-type="bibr" rid="B38">Mooney et al., 2020</xref>; <xref ref-type="bibr" rid="B24">Lamont et al., 2022a</xref>).</p>
<p>Traditional methods of diver surveys are still the most widely accepted and standardized method for reef monitoring (i.e., AGRRA surveys), but come with limitations. Visual transect surveys can be time- and resource-consuming, provide only intermittent snapshots of reef state, and potentially introduce bias through observer limitations and fish deterrence (<xref ref-type="bibr" rid="B9">Brock, 1982</xref>; <xref ref-type="bibr" rid="B55">Sale and Sharp, 1983</xref>). However, the great diversity and concentration of soniferous species on reefs, as well as those that make ancillary sounds, contribute to an active, bustling soundscape that makes coral reefs excellent candidates for passive acoustic monitoring (PAM; <xref ref-type="bibr" rid="B39">Mooney et al., 2020</xref>; <xref ref-type="bibr" rid="B22">Kaplan et al., 2018</xref>). Changes to the community assemblages, such as that which exists between neighboring locations (<xref ref-type="bibr" rid="B52">Radford et al., 2014</xref>) or after severe habitat degradation (<xref ref-type="bibr" rid="B19">Gordon et al., 2018</xref>) can be detected in the soundscape. The potential for non-invasive continuous monitoring in these critical ecosystems, paired with the relative accessibility and low cost of PAM, makes further investigation into meaningful acoustic metrics for coral reef health imperative.</p>
<p>Sound is a dynamic component of coral reef communities. The two persistent sources of biological sounds on coral reefs are marine invertebrates, particularly snapping shrimp, which occupy the mid-to high-frequencies (&#x223c;2&#x2013;20&#xa0;kHz) (<xref ref-type="bibr" rid="B3">Au and Banks, 1998</xref>), and lower frequency fish sounds, typically below 2&#xa0;kHz (<xref ref-type="bibr" rid="B63">Tricas and Boyle, 2014</xref>; <xref ref-type="bibr" rid="B16">Ferguson et al., 2022</xref>). Soundscape signatures can vary on daily (<xref ref-type="bibr" rid="B59">Staaterman et al., 2014</xref>; <xref ref-type="bibr" rid="B23">Kaplan et al., 2015</xref>), celestial, (<xref ref-type="bibr" rid="B59">Staaterman et al., 2014</xref>; <xref ref-type="bibr" rid="B46">Parsons et al., 2016</xref>; <xref ref-type="bibr" rid="B35">McWilliam et al., 2017</xref>), and seasonal scales (<xref ref-type="bibr" rid="B22">Kaplan et al., 2018</xref>), and are biologically important for coral reef animals. Sounds are produced for communicative purposes, such as for courtship and reproduction (<xref ref-type="bibr" rid="B42">Myrberg et al., 1986</xref>; <xref ref-type="bibr" rid="B74">Parmentier et al., 2010</xref>; <xref ref-type="bibr" rid="B63">Tricas and Boyle, 2014</xref>), aggression (<xref ref-type="bibr" rid="B74">Parmentier et al., 2010</xref>; <xref ref-type="bibr" rid="B63">Tricas and Boyle, 2014</xref>), and territory defense (<xref ref-type="bibr" rid="B71">Winn et al., 1964</xref>; <xref ref-type="bibr" rid="B41">Myrberg, 1997</xref>), as well as incidentally, by feeding (<xref ref-type="bibr" rid="B72">Sartori and Bright, 1973</xref>). These cues can then be perceived and utilized by reef animals. Indeed, evidence suggests juvenile and larval fish use sound to relocate and orient themselves to reefs (<xref ref-type="bibr" rid="B37">Montgomery et al., 2006</xref>; <xref ref-type="bibr" rid="B56">Simpson et al., 2008</xref>; <xref ref-type="bibr" rid="B53">Radford et al., 2011</xref>; <xref ref-type="bibr" rid="B60">Suca et al., 2020</xref>) and coral larvae use sound as a settlement cue for suitable habitat (<xref ref-type="bibr" rid="B27">Lillis et al., 2016</xref>; <xref ref-type="bibr" rid="B26">Lillis et al., 2018</xref>; <xref ref-type="bibr" rid="B1">Aoki et al., 2024</xref>). While increasingly applied to soundscape metrics, how these various soundscape components can be used to assess habitat and community attributes is still being understood.</p>
<p>Snapping shrimp band average sound pressure level (SPL) and snap counts have been shown to be indicative of structural complexity, but not necessarily fish community, live coral cover, or overall reef health (<xref ref-type="bibr" rid="B23">Kaplan et al., 2015</xref>; <xref ref-type="bibr" rid="B43">Nedelec et al., 2015</xref>; <xref ref-type="bibr" rid="B31">Lyon et al., 2019</xref>; <xref ref-type="bibr" rid="B68">Williams et al., 2022</xref>). Low frequency SPL is among the most common analyses for fish sounds, but its effectiveness in predicting reef health has yielded mixed results. In some studies, higher sound levels below 2&#xa0;kHz, along with increased sound levels around dawn and dusk, were correlated with higher coral cover and fish abundance (<xref ref-type="bibr" rid="B48">Piercy et al., 2014</xref>; <xref ref-type="bibr" rid="B23">Kaplan et al., 2015</xref>; <xref ref-type="bibr" rid="B47">Peck et al., 2021</xref>). Yet in other studies, low frequency SPL alone had little relationship with reef composition (<xref ref-type="bibr" rid="B25">Lamont et al., 2022b</xref>; <xref ref-type="bibr" rid="B68">Williams et al., 2022</xref>) or had partial or mixed success (<xref ref-type="bibr" rid="B4">Bertucci et al., 2016</xref>; <xref ref-type="bibr" rid="B11">Dimoff et al., 2021</xref>). Additionally, while fish call rates have revealed similar trends to low frequency SPL at a single site, <xref ref-type="bibr" rid="B16">Ferguson et al. (2022)</xref> showed that the direct relationship between these two variables was not significant. Fewer studies have examined the daily fluctuations in SPL, despite documented increases in fish sound production around dawn and dusk (<xref ref-type="bibr" rid="B71">Winn et al., 1964</xref>; <xref ref-type="bibr" rid="B74">Parmentier et al., 2010</xref>).</p>
<p>Other processing techniques often derived from terrestrial applications have been proposed to address marine biodiversity questions (<xref ref-type="bibr" rid="B61">Sueur et al., 2008a</xref>), yet they too have borne challenges. A major appeal to exploring these indices is their potential application to uncalibrated sound recordings, which, if successful, opens the door to low-cost recording alternatives (<xref ref-type="bibr" rid="B24">Lamont et al., 2022a</xref>). Unfortunately, the success of these indices in determining coral reef health has been wildly variable between locations and applications. The Acoustic Complexity Index (ACI; <xref ref-type="bibr" rid="B50">Pieretti et al., 2011</xref>) is the most popular index in marine environments (<xref ref-type="bibr" rid="B49">Pieretti and Danovaro, 2020</xref>; <xref ref-type="bibr" rid="B36">Minello et al., 2021</xref>) and has shown promise in the lower frequency fish band in some studies. In certain cases, ACI demonstrated robustness to wind and boat noise (<xref ref-type="bibr" rid="B21">Harris et al., 2016</xref>) and outperformed alternative metrics in its ability to predict environment or reef state (<xref ref-type="bibr" rid="B59">Staaterman et al., 2014</xref>; <xref ref-type="bibr" rid="B25">Lamont et al., 2022b</xref>; <xref ref-type="bibr" rid="B32">Mahale et al., 2023</xref>). Yet in similar studies, it was not a significant predictor of reef quality (<xref ref-type="bibr" rid="B23">Kaplan et al., 2015</xref>; <xref ref-type="bibr" rid="B31">Lyon et al., 2019</xref>) or species diversity (<xref ref-type="bibr" rid="B58">Staaterman et al., 2017</xref>). Specific parameters play a role in the effectiveness of ACI and other indices but are not standardized and optimized specifications likely vary by location (<xref ref-type="bibr" rid="B21">Harris et al., 2016</xref>; <xref ref-type="bibr" rid="B8">Bolgan et al., 2018</xref>; <xref ref-type="bibr" rid="B11">Dimoff et al., 2021</xref>). Further, in many of these applications, we still lack ground-truthing of these metrics to specific call types, rates, and at times, even local observations of fish and reef communities, thus metric applications were often correlative.</p>
<p>This study evaluated whether the number of low frequency biotic sounds could function as a proxy for fish abundance and coral cover at different sites with varying communities, leveraging the known positive correlation between these two variables (<xref ref-type="bibr" rid="B73">Komyakova et al., 2013</xref>). We sought to test the hypothesis that between-site variations in total acoustic energy in the low frequency band are a result of differential fish activity and abundance (e.g., <xref ref-type="bibr" rid="B23">Kaplan et al., 2015</xref>). To do so, acoustic recordings from three long-term studied coral reefs of varying community assemblages in the U.S. Virgin Islands were manually audited for presumed fish sounds. The strength of crepuscular activity spikes and average call rates were examined and compared for each site. Hard coral coverage and fish abundance for each reef were collected from parallel and ongoing efforts and used to ground-truth acoustic outputs [<xref ref-type="bibr" rid="B12">Dinh et al., 2018</xref>; Formel et al. (in preparation)]. Further, this study compared fish call rates to a variety of acoustic metrics and indices typically used in the bioacoustic literature, including SPL, ACI, acoustic entropy (H), the bioacoustic index (BIO), acoustic diversity (ADI), and acoustic evenness (AEI), to evaluate their effectiveness in predicting reef community assemblages.</p>
</sec>
<sec sec-type="materials|methods" id="s2">
<title>2 Methods and materials</title>
<sec id="s2-1">
<title>2.1 Data collection</title>
<p>Three sites with long-term acoustic and visual monitoring were selected in the U.S. Virgin Islands National Park on St. John, USVI, based on their varying coral cover and fish abundance (<xref ref-type="fig" rid="F1">Figure 1A</xref>). These fringing coastal reefs are part of a long-term project aiming to understand the relationship between soundscapes and the reef community (<xref ref-type="bibr" rid="B23">Kaplan et al., 2015</xref>; <xref ref-type="bibr" rid="B39">Mooney et al., 2017</xref>). Summaries of the reef community assessments are briefly described below but can be found in more detail in earlier work (<xref ref-type="bibr" rid="B23">Kaplan et al., 2015</xref>; <xref ref-type="bibr" rid="B12">Dinh et al., 2018</xref>; Formel et al. [in preparation]). Tektite Reef (18.30962 N, 64.72218&#xa0;W) is considered an acoustically rich reef, correlating with high fish diversity and coral cover (<xref ref-type="bibr" rid="B23">Kaplan et al., 2015</xref>; <xref ref-type="bibr" rid="B16">Ferguson et al., 2022</xref>; <xref ref-type="table" rid="T1">Table 1</xref>). Yawzi Point (18.31458 N, 64.72609&#xa0;W) was selected as an intermediate quality reef and is characterized by slightly lower fish abundances and diversity (<xref ref-type="bibr" rid="B18">Friedlander and Beets, 2008</xref>) and generally lower hard coral cover (<xref ref-type="bibr" rid="B14">Edmunds, 2013</xref>; <xref ref-type="table" rid="T1">Table 1</xref>). Finally, Cocoloba Reef (18.31528 N, 64.76065&#xa0;W) was a degraded reef habitat increasingly dominated by macroalgae and bare space (<xref ref-type="table" rid="T1">Table 1</xref>), with historically low fish diversity (<xref ref-type="bibr" rid="B18">Friedlander and Beets, 2008</xref>).</p>
<fig id="F1" position="float">
<label>FIGURE 1</label>
<caption>
<p>
<bold>(A)</bold> Map of the three study reefs on the south side of St. John, US Virgin Islands, located within the Virgin Islands National Park. <bold>(B)</bold> ST-300 single channel recorder located on Tektite reef. The same set-up was used for Yawzi sound recordings as well. <bold>(C)</bold> ST-4300 four channel recorder on Cocoloba. Only the first channel was used for analysis.</p>
</caption>
<graphic xlink:href="frsen-05-1338586-g001.tif"/>
</fig>
<table-wrap id="T1" position="float">
<label>TABLE 1</label>
<caption>
<p>Bottom composition of the three sites based on point intercept transect surveys averaged across 2016&#x2013;2017 (Tektite n &#x3d; 12, Yawzi n &#x3d; 13, Cocoloba n &#x3d; 12). Values are percentages of total recorded bottom cover. Methods adapted from Atlantic and Gulf Rapid Reef Assessment (AGRRA) surveys, following Formel et al. (in preparation, 2023).</p>
</caption>
<table>
<thead valign="top">
<tr>
<th align="left"/>
<th align="left">Hard coral (%)</th>
<th align="left">Algae (%)</th>
<th align="left">Crustose coralline algae (%)</th>
<th align="left">Cyanobacteria (%)</th>
<th align="left">Soft coral (%)</th>
<th align="left">Sponge (%)</th>
<th align="left">Other biotic (%)</th>
<th align="left">Abiotic (%)</th>
</tr>
</thead>
<tbody valign="top">
<tr>
<td align="left">Tektite</td>
<td align="left">25.58</td>
<td align="left">43.75</td>
<td align="left">3.50</td>
<td align="left">6.17</td>
<td align="left">1.42</td>
<td align="left">7.92</td>
<td align="left">0.33</td>
<td align="left">17.41</td>
</tr>
<tr>
<td align="left">Yawzi</td>
<td align="left">14.06</td>
<td align="left">33.52</td>
<td align="left">2.42</td>
<td align="left">0.99</td>
<td align="left">6.94</td>
<td align="left">5.36</td>
<td align="left">1.94</td>
<td align="left">34.44</td>
</tr>
<tr>
<td align="left">Cocoloba</td>
<td align="left">4.92</td>
<td align="left">47.00</td>
<td align="left">1.00</td>
<td align="left">0.33</td>
<td align="left">4.50</td>
<td align="left">0.58</td>
<td align="left">0.42</td>
<td align="left">41.67</td>
</tr>
</tbody>
</table>
</table-wrap>
<p>Video transect surveys were conducted to assess fish abundance and diversity at each site in June 2016 and July 2017 (methods following <xref ref-type="bibr" rid="B12">Dinh et al., 2018</xref>). Each 30&#xa0;m transect was recorded and analyzed in the lab to quantify the number of species and number of total fish in each video (<xref ref-type="bibr" rid="B12">Dinh et al., 2018</xref>). While the visual surveys did not precisely co-occur with our acoustic surveys, the goal was to determine how the sites generally differed in community composition, rather than document subtle fluctuations in fish populations during the study period. Further, while some fish movements are to be expected, many reef fish are known for their high site fidelity and dramatic relocations are unlikely within a year (<xref ref-type="bibr" rid="B34">Marnane, 2000</xref>; <xref ref-type="bibr" rid="B51">Pittman et al., 2014</xref>; <xref ref-type="bibr" rid="B20">Griffin et al., 2023</xref>). The resulting species numbers and counts for 9 transects per site were averaged, and site means were used to compare with acoustic metrics. Distribution of both species and total fish were normal, so an ANOVA, followed by a Tukey HSD <italic>post hoc</italic> test, was used for statistical comparison between sites. Parallel to fish, the benthic composition of each site was characterized using manual surveys following Atlantic and Gulf Rapid Reef Assessment (AGRRA) methods (following Formel et al. [in preparation]). Diver transects at Tektite (n &#x3d; 12), Cocoloba (n &#x3d; 12), and Yawzi (n &#x3d; 13) were averaged across 2016 and 2017 to quantify the benthic coverage percentage of hard coral, macroalgae, crustose coralline algae, cyanobacteria, soft coral, sponge, other biotic, and abiotic for each site (<xref ref-type="table" rid="T1">Table 1</xref>). The hard coral coverage difference between sites was statistically assessed with an ANOVA, followed by a Tukey HSD <italic>post hoc</italic> test.</p>
<p>Sound data from Tektite and Yawzi were collected on single-channel SoundTraps (ST-300; Ocean Instruments, sensitivity &#x3d; &#x2212;172.6 and &#x2212;171.2&#xa0;dB re 1&#xa0;&#x3bc;Pa/V, respectively <xref ref-type="fig" rid="F1">Figure 1B</xref>). Cocoloba data were collected with a 4-channel ST-4300 recorder (Ocean Instruments, sensitivity &#x3d; &#x2212;161.2&#xa0;dB re 1&#xa0;&#x3bc;Pa/V <xref ref-type="fig" rid="F1">Figure 1C</xref>); only one channel was used for fish call audits and batch analyses. Instruments were secured 0.5&#xa0;m above the seafloor on rebar stakes anchored in sandy patches within the reef (<xref ref-type="fig" rid="F1">Figure 1</xref>). SoundTraps were deployed from March 2017 to July 2017, recording on a duty cycle of 3&#xa0;s of self-calibration followed by 60&#xa0;s of recording every 10&#xa0;min at 48&#xa0;kHz.</p>
</sec>
<sec id="s2-2">
<title>2.2 Fish call auditing</title>
<p>Due to the labor-intensive nature of selecting fish calls by hand, 8 days of the 2017 spring and early summer deployment were chosen for analysis and 1&#xa0;minute every 30&#xa0;min was manually audited for fish vocalizations. To account for the possible effect of the moon phase on fish call rates (<xref ref-type="bibr" rid="B46">Parsons et al., 2016</xref>; <xref ref-type="bibr" rid="B35">McWilliam et al., 2017</xref>), days of interest were selected at various points in the lunar cycle: full moon (11 April, 10 May), third quarter (19 April, 18 May), new moon (26 April, 25 May), and first-quarter (2 May, 1 June).</p>
<p>The resulting 24 days (8 days for 3 sites) of subsampled sound data was manually analyzed by 3 independent, trained analysts (S.D.J., N.F., S.R.F.) using a customized interactive interface created in MATLAB R2020A (Mathworks, Natick, MA). First, sound files were low-pass filtered and decimated to 4&#xa0;kHz to focus on the lower frequency range typical of fish calls. Nearly all reef fish sounds are below 2000&#xa0;Hz, particularly between 50 and 1,200&#xa0;Hz (<xref ref-type="bibr" rid="B63">Tricas and Boyle, 2014</xref>; <xref ref-type="bibr" rid="B16">Ferguson et al., 2022</xref>; <xref ref-type="bibr" rid="B54">Rice et al., 2022</xref>), which was the focus of this study. Spectrograms were then created (128&#xa0;pt, 32&#xa0;ms Hamming window, 75% overlap, 1,024&#xa0;pt FFT size) and visualized in 10-s increments to distinguish characteristically short-duration fish calls (<xref ref-type="bibr" rid="B63">Tricas and Boyle, 2014</xref>). Analysts boxed fish calls by time and frequency and defined them as &#x201c;pulse&#x201d; or &#x201c;tonal&#x201d;, or &#x201c;chorus&#x201d; &#x2013; in the case of overlapping, indistinguishable vocal events. The &#x201c;chorus&#x201d; label was used sparingly when individual calls were impossible to isolate and were thus factored into the final counts as only a single call, inevitably underrepresenting high activity periods to some extent. Final checks over all the annotations were done for consistency by S.D.J.</p>
<p>Any high-amplitude abiotic noise, such as weather or vessels, that had the potential to interfere with fish call detection was also boxed and labeled. Later, periods of disrupting noise were removed from the analysis, subtracting the entire period from both the call counts and the time available.</p>
</sec>
<sec id="s2-3">
<title>2.3 Analysis</title>
<p>Data preparation, statistical analysis, and graphing were done in MATLAB R2020b and R (<ext-link ext-link-type="uri" xlink:href="http://www.r-project.org">www.r-project.org</ext-link>). Call rates were first calculated for each 1-min segment by dividing the total number of calls by the number of seconds available, after any vessel or disruptive noise was removed. If less than 10&#xa0;s of useable data remained, the whole segment was removed from all analyses.</p>
<p>All site-specific total averages, such as for visual measures, fish call rates, or received SPL, are reported as mean &#xb1; 1.96&#x2a;standard error (SE), which represent the upper and lower bounds of 95% confidence intervals of the mean. To visually compare trends between sites on a daily scale, hourly call rates were first calculated and then all 8&#xa0;days were averaged together at each hour of the day. To examine the effect of time of day further, each day was divided into 4 time periods based on their respective local daily light periods, downloaded from <ext-link ext-link-type="uri" xlink:href="http://timeanddate.com">timeanddate.com</ext-link>. Time-of-day groupings were delineated as follows: dusk: from sunset to astronomical twilight (defined as when the center of the Sun is eighteen degrees below the horizon, <xref ref-type="bibr" rid="B17">Forsythe et al., 1995</xref>), night: time between the two astronomical twilights, dawn:from astronomical twilight to sunrise, and day: from sunrise to sunset. The average call rate, in calls per minute, was calculated for each time period first for each moon phase and then combined, by averaging call rates from all files within each time-of-day period. A ratio of change was measured to evaluate the strength of crepuscular peaks by site, by dividing the average call rate in the crepuscular time periods by their adjacent daily period. Thus, values of 1 indicate no change between successive light periods, with higher ratios denoting larger shifts in acoustic activity.</p>
<p>Within-site comparisons of time-of-day on call rate required transformations to achieve normality, and then were evaluated with a one-way ANOVA. If significant differences were found, Tukey&#x2019;s HSD <italic>post hoc</italic> test, with no multiple comparisons correction, was performed to identify where these differences lay. Tektite and Yawzi both used a square root transformation, but Cocoloba only met the assumptions after a simple logarithmic transformation (there were no zero data points at any site). Transformations remained consistent within their respective site between each moon phase tested. Between-site comparisons for both cumulative and for each daily light period were assessed with a Kruskal&#x2013;Wallis test (KW) on untransformed data, followed by Dunn&#x2019;s test of multiple comparisons, with no adjustment. Results from both the ANOVA and KW, along with associated <italic>post hoc</italic> tests, are summarized in <xref ref-type="table" rid="T2">Tables 2</xref>, <xref ref-type="table" rid="T3">3</xref> for ease of understanding.</p>
<table-wrap id="T2" position="float">
<label>TABLE 2</label>
<caption>
<p>Results of Kruskal&#x2013;Wallis non-parametric analysis of variance on call rates (calls/min) between sites at different times of day. Each significant light period was followed up with Dunn&#x2019;s test for multiple comparisons, with no adjustment. Z-statistics and <italic>p</italic>-values are listed for each combination of sites. Significant <italic>p</italic>-values are indicated with stars (&#x2a;<italic>p</italic> &#x3c; 0.05; &#x2a;&#x2a;<italic>p</italic> &#x3c; 0.01; &#x2a;&#x2a;&#x2a;<italic>p</italic> &#x3c; 0.001).</p>
</caption>
<table>
<thead valign="top">
<tr>
<th rowspan="2" align="left"/>
<th colspan="3" align="center">Kruskal&#x2013;Wallis test (between-site differences in call rates for each daily period)</th>
<th colspan="3" align="center">Dunn&#x2019;s test (pairwise site comparison)</th>
</tr>
<tr>
<th align="center">
<italic>X</italic>
<sup>
<italic>2</italic>
</sup>
</th>
<th align="center">DF</th>
<th align="center">
<italic>p</italic>-value</th>
<th align="center">Tektite-Yawzi</th>
<th align="center">Tektite-Cocoloba</th>
<th align="center">Yawzi-Cocoloba</th>
</tr>
</thead>
<tbody valign="top">
<tr>
<td rowspan="2" align="center">Night</td>
<td rowspan="2" align="center">176</td>
<td rowspan="2" align="center">2</td>
<td rowspan="2" align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">z &#x3d; 10.2</td>
<td align="center">z &#x3d; &#x2212;12.5</td>
<td align="center">z &#x3d; &#x2212;2.07</td>
</tr>
<tr>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a;</td>
</tr>
<tr>
<td rowspan="2" align="center">Dawn</td>
<td rowspan="2" align="center">29.2</td>
<td rowspan="2" align="center">2</td>
<td rowspan="2" align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">z &#x3d; 4.00</td>
<td align="center">z &#x3d; &#x2212;5.18</td>
<td align="center">z &#x3d; &#x2212;1.15</td>
</tr>
<tr>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3d; 0.13</td>
</tr>
<tr>
<td rowspan="2" align="center">Day</td>
<td rowspan="2" align="center">131</td>
<td rowspan="2" align="center">2</td>
<td rowspan="2" align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">z &#x3d; 5.94</td>
<td align="center">z &#x3d; &#x2212;11.4</td>
<td align="center">z &#x3d; &#x2212;5.33</td>
</tr>
<tr>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
</tr>
<tr>
<td rowspan="2" align="center">Dusk</td>
<td rowspan="2" align="center">15.1</td>
<td rowspan="2" align="center">2</td>
<td rowspan="2" align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">z &#x3d; 1.75</td>
<td align="center">z &#x3d; &#x2212;3.89</td>
<td align="center">z &#x3d; &#x2212;2.09</td>
</tr>
<tr>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a;</td>
</tr>
<tr>
<td rowspan="2" align="center">Total</td>
<td rowspan="2" align="center">330</td>
<td rowspan="2" align="center">2</td>
<td rowspan="2" align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">z &#x3d; 11.8</td>
<td align="center">z &#x3d; &#x2212;17.9</td>
<td align="center">z &#x3d; &#x2212;5.74</td>
</tr>
<tr>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a;</td>
</tr>
</tbody>
</table>
</table-wrap>
<table-wrap id="T3" position="float">
<label>TABLE 3</label>
<caption>
<p>Results from one-way ANOVA tests comparing within-site daily call rate changes, across different lunar cycles. If significance (<italic>p</italic> &#x3c; 0.05) was found, <italic>post hoc</italic> Tukey HSD tests were performed. Otherwise, no difference was reported. Difference ratios (% diff) were calculated for overall sites when significance was reported from the Tukey HSD test by dividing the average call rate from the higher period (listed first) by the lower period.</p>
</caption>
<table>
<thead valign="top">
<tr>
<th rowspan="2" align="left"/>
<th colspan="3" align="center">ANOVA</th>
<th colspan="6" align="center">Tukey HSD results</th>
</tr>
<tr>
<th align="center">
<italic>F</italic>-value</th>
<th align="center">DF</th>
<th align="center">
<italic>p</italic>-value</th>
<th align="center">Dusk-night</th>
<th align="center">Dawn-night</th>
<th align="center">Day-night</th>
<th align="center">Dawn-day</th>
<th align="center">Dusk-day</th>
<th align="center">Dawn-dusk</th>
</tr>
</thead>
<tbody valign="top">
<tr>
<td align="left">Tektite</td>
<td align="center">7.17</td>
<td align="center">3,336</td>
<td align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3d; 0.23</td>
<td align="center">
<italic>p</italic> &#x3d; 0.098</td>
<td align="center">
<italic>p</italic> &#x3d; 0.065</td>
<td align="center">
<italic>p</italic> &#x3c; 0.005&#x2a;&#x2a; % diff &#x3d; 1.36</td>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a; % diff &#x3d; 1.36</td>
<td align="center">
<italic>p</italic> &#x3d; 0.98</td>
</tr>
<tr>
<td align="right">Full</td>
<td align="center">1.33</td>
<td align="center">3.78</td>
<td align="center">0.335</td>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
</tr>
<tr>
<td align="right">Third-Q</td>
<td align="center">0.319</td>
<td align="center">3.82</td>
<td align="center">0.812</td>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
</tr>
<tr>
<td align="right">New</td>
<td align="center">6.54</td>
<td align="center">3.82</td>
<td align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3d; 0.95</td>
<td align="center">
<italic>p</italic> &#x3d; 0.14</td>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.005&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3d; 0.17</td>
<td align="center">
<italic>p</italic> &#x3d; 0.77</td>
</tr>
<tr>
<td align="right">First-Q</td>
<td align="center">8.08</td>
<td align="center">3.78</td>
<td align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3d; 0.26</td>
<td align="center">
<italic>p</italic> &#x3d; 0.23</td>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.01&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3d; 0.99</td>
</tr>
<tr>
<td align="left">Yawzi</td>
<td align="center">13.1</td>
<td align="center">3,330</td>
<td align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a; % diff &#x3d; 1.38</td>
<td align="center">
<italic>p</italic> &#x3c; 0.01&#x2a;&#x2a; % diff &#x3d; 1.69</td>
<td align="center">
<italic>p</italic> &#x3c; 0.001&#x2a;&#x2a;&#x2a; % diff &#x3d; 1.21</td>
<td align="center">
<italic>p</italic> &#x3d; 0.42</td>
<td align="center">
<italic>p</italic> &#x3c; 0.005&#x2a;&#x2a; % diff &#x3d; 1.14</td>
<td align="center">
<italic>p</italic> &#x3d; 0.30</td>
</tr>
<tr>
<td align="right">Full</td>
<td align="center">2.16</td>
<td align="center">3.79</td>
<td align="center">0.099</td>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
</tr>
<tr>
<td align="right">Third-Q</td>
<td align="center">7.13</td>
<td align="center">3.78</td>
<td align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.01&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.01&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3d; 0.17</td>
<td align="center">
<italic>p</italic> &#x3d; 0.14</td>
<td align="center">
<italic>p</italic> &#x3d; 0.99</td>
</tr>
<tr>
<td align="right">New</td>
<td align="center">2.43</td>
<td align="center">3.79</td>
<td align="center">0.071</td>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
</tr>
<tr>
<td align="right">First-Q</td>
<td align="center">6.06</td>
<td align="center">3.82</td>
<td align="center">&#x3c;0.001&#x2a;&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.005&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3d; 0.80</td>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3d; 0.98</td>
<td align="center">
<italic>p</italic> &#x3d; 0.10</td>
<td align="center">
<italic>p</italic> &#x3d; 0.22</td>
</tr>
<tr>
<td align="left">Cocoloba</td>
<td align="center">4.89</td>
<td align="center">3,363</td>
<td align="center">&#x3c;0.005&#x2a;&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a; % diff &#x3d; 1.29</td>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a; % diff &#x3d; 1.36</td>
<td align="center">
<italic>p</italic> &#x3d; 0.26</td>
<td align="center">
<italic>p</italic> &#x3d; 0.13</td>
<td align="center">
<italic>p</italic> &#x3d; 0.22</td>
<td align="center">
<italic>p</italic> &#x3d; 0.99</td>
</tr>
<tr>
<td align="right">Full</td>
<td align="center">0.756</td>
<td align="center">3.85</td>
<td align="center">0.52</td>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
</tr>
<tr>
<td align="right">Third-Q</td>
<td align="center">1.97</td>
<td align="center">3.88</td>
<td align="center">0.12</td>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
</tr>
<tr>
<td align="right">New</td>
<td align="center">1.73</td>
<td align="center">3.87</td>
<td align="center">0.17</td>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
<td align="left"/>
</tr>
<tr>
<td align="right">First-Q</td>
<td align="center">3.06</td>
<td align="center">3.90</td>
<td align="center">&#x3c;0.05&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3c; 0.05&#x2a;</td>
<td align="center">
<italic>p</italic> &#x3d; 0.62</td>
<td align="center">
<italic>p</italic> &#x3d; 0.43</td>
<td align="center">
<italic>p</italic> &#x3d; 0.97</td>
<td align="center">
<italic>p</italic> &#x3d; 0.13</td>
<td align="center">
<italic>p</italic> &#x3d; 0.52</td>
</tr>
</tbody>
</table>
</table-wrap>
<p>Received SPL in the fish band was calculated from each audited sound file, with vessel noise durations removed, by bandpass filtering from 50 to 1,200&#xa0;Hz. The 60&#xa0;s signal was divided into blocks of 1&#xa0;s with 50% overlap, root-mean-squared SPL was calculated and averaged across all blocks in that sound file, and finally converted to decibels (dB). Statistical average SPL was then calculated hourly and for each daily light period in order to examine crepuscular trends for each site. Statistical means and standard errors reported here do not operate on the linear units and thus do not represent the total noise energy, however, they more appropriately describe the underlying statistical distribution of noise levels. Comparison between the two methods revealed less than a dB of difference for overall site means. For analogous arithmetic calculations using linear units of SPL, see the <xref ref-type="sec" rid="s10">Supplementary Material</xref>.</p>
<p>Several acoustic indices were also calculated from audited files to compare directly to fish call counts, using <italic>Seewave</italic> (<xref ref-type="bibr" rid="B61">Sueur et al., 2008a</xref>) and <italic>Soundecology</italic> (<xref ref-type="bibr" rid="B65">Villanueva-Rivera and Pijanowski, 2018</xref>) packages in R (methods following <xref ref-type="bibr" rid="B68">Williams et al., 2022</xref>). Given the clear characterization of fish call rates, we sought to test and evaluate the effectiveness of several acoustic indices that have been suggested to help quantify aquatic biodiversity. The indices tested were the Acoustic Complexity Index (ACI), which quantifies the variability of intensities in each frequency bin (window length &#x3d; 512, overlap &#x3d; 0, window &#x3d; Hamming, frequency range &#x3d; 50&#xa0;Hz&#x2013;1,200&#xa0;Hz; <xref ref-type="bibr" rid="B50">Pieretti et al., 2011</xref>); Acoustic Entropy (H), the product of temporal and spectral dissimilarities (window length &#x3d; 512, envelope transform &#x3d; Hilbert; <xref ref-type="bibr" rid="B62">Sueur et al., 2008b</xref>); the Bioacoustic Index (BIO), a calculation of both the sound amplitude and number of frequency bands occupied (freq range &#x3d; 50&#xa0;Hz&#x2013;1,200&#xa0;Hz, dB threshold &#x3d; &#x2212;50, freq step &#x3d; 100; <xref ref-type="bibr" rid="B6">Boelman et al., 2007</xref>); the Acoustic Diversity Index, in which the Shannon index is applied to frequency bins over a specified threshold (ADI, Max freq &#x3d; 1,200, dB threshold &#x3d; &#x2212;50, freq step &#x3d; 100, <xref ref-type="bibr" rid="B66">Villanueva-Rivera et al., 2011</xref>); and the Acoustic Evenness Index, a measure of the proportion of frequency bins over a specified threshold (AEI, Max freq &#x3d; 1,200&#xa0;Hz; freq step &#x3d; 200; threshold &#x3d; &#x2212;50 dB, <xref ref-type="bibr" rid="B66">Villanueva-Rivera et al., 2011</xref>).</p>
<p>Distributions of SPL and acoustic indices were strongly non-normal, so a Kruskal&#x2013;Wallis followed by Dunn&#x2019;s test with a Bonferroni correction was applied to compare between sites. Linear regressions were utilized to evaluate the relationship between call rate and acoustic indices for each sound file, as well as relationships between SPL and other indices. Kendall&#x2019;s tau (&#x3c4;) coefficient was chosen as a non-parametric alternative to calculate the correlation between acoustic metrics and visual metrics. A complete correlation matrix between all acoustic and visual relationships can be found in the <xref ref-type="sec" rid="s10">Supplementary Material</xref>. Overall site averages across 2016&#x2013;2017 transects were used to represent fish abundance, fish species richness, and hard coral cover percentage for the correlation analysis.</p>
</sec>
</sec>
<sec sec-type="results" id="s3">
<title>3 Results</title>
<sec id="s3-1">
<title>3.1 Reef biometrics</title>
<p>The three reefs varied by hard coral coverage (<xref ref-type="table" rid="T1">Table 1</xref>, One-way ANOVA: F<sub>2,34</sub> &#x3d; 35.12, <italic>p</italic> &#x3c; 0.0001), fish abundance (<xref ref-type="fig" rid="F2">Figure 2</xref>, One-way ANOVA: F<sub>2,24</sub> &#x3d; 19.0, <italic>p</italic> &#x3c; 0.0001), and fish species richness (<xref ref-type="fig" rid="F2">Figure 2</xref>, One-way ANOVA: F<sub>2,24</sub> &#x3d; 12.3, <italic>p</italic> &#x3c; 0.0005). Tektite had the highest coral coverage (25.58% &#xb1; 2.78%, mean &#xb1; 1.96&#x2a;SE), highest average number of total fish (175.5 &#xb1; 15.4), and most fish species (22.8 &#xb1; 1.0) per transect. As determined by a Tukey&#x2019;s <italic>post hoc</italic> test, this was significantly higher than the degraded site, Cocoloba, which had the lowest coral cover (4.92% &#xb1; 3.10%, <italic>p</italic> &#x3c; 0.0001), total fish (43.8 &#xb1; 4.5, <italic>p</italic> &#x3c; 0.001), and species per transect (13.6 &#xb1; 0.4, <italic>p</italic> &#x3c; 0.0001). Yawzi had the second highest coral cover (14.06% &#xb1; 2.40%), fish abundance (141.8 &#xb1; 14.9), and richness (20.1 &#xb1; 0.4 species), also significantly higher than Cocoloba (Tukey <italic>post hoc</italic>, coral: <italic>p</italic> &#x3c; 0.005, total fish: <italic>p</italic> &#x3c; 0.005, species: <italic>p</italic> &#x3c; 0.001). Despite the differences, Yawzi was not significantly different from Tektite in fish abundance and species counts but did significantly differ in hard coral coverage (Tukey&#x2019;s <italic>post hoc</italic>, <italic>p</italic> &#x3c; 0.0005).</p>
<fig id="F2" position="float">
<label>FIGURE 2</label>
<caption>
<p>Results of manual video transect analysis of fish species and total counts at Tektite, Yawzi, and Cocoloba reefs from 2016 to 2017, showing site differences in community assemblage. Each analyzed 30&#xa0;m transect is represented by a point.</p>
</caption>
<graphic xlink:href="frsen-05-1338586-g002.tif"/>
</fig>
</sec>
<sec id="s3-2">
<title>3.2 Call rates</title>
<p>A total of 1,041 manually audited 1-min sound files were analyzed between the three sites after boat noise was removed (Tektite: 340, Yawzi: 334, Cocoloba: 367). A KW test revealed significant differences between total call rates at the three sites (<italic>X</italic>
<sup>
<italic>2</italic>
</sup>(2) &#x3d; 330, <italic>p</italic> &#x3c; 0.001). Tektite had the highest average call rate, with 63.93 &#xb1; 0.16 calls per minute, significantly greater than the next highest, Yawzi, at 39.16 &#xb1; 1.67 calls per minute, during all photoperiods (<xref ref-type="fig" rid="F3">Figure 3</xref>; <xref ref-type="table" rid="T2">Table 2</xref>) and Cocoloba, which had the lowest average call rate at 31.67 &#xb1; 0.08 calls per minute (<xref ref-type="fig" rid="F3">Figure 3</xref>; <xref ref-type="table" rid="T2">Table 2</xref>). Yawzi recorded higher call rates than Cocoloba in all photoperiods, with this relationship showing significance during night, day, and dusk (<xref ref-type="fig" rid="F3">Figure 3</xref>; <xref ref-type="table" rid="T2">Table 2</xref>).</p>
<fig id="F3" position="float">
<label>FIGURE 3</label>
<caption>
<p>Comparison of call rate by reef during four daily photoperiods, demonstrating variation in crepuscular activity between sites. Points represent averaged call rate for each daily period by moon phase, with 95% confidence interval bars (&#xb1;1.96&#x2a;SE), colored by site. Mean call rate for each photoperiod and site is visualized by a horizontal dashed line. Significant difference in call rates between pairs of sites is shown with stars (&#x2a;<italic>p</italic> &#x3c; 0.05; &#x2a;&#x2a;<italic>p</italic> &#x3c; 0.01; &#x2a;&#x2a;&#x2a;<italic>p</italic> &#x3c; 0.001, Dunn&#x2019;s test for multiple comparisons, no adjustment).</p>
</caption>
<graphic xlink:href="frsen-05-1338586-g003.tif"/>
</fig>
<p>Some degree of crepuscular activity spikes was observed at all sites (<xref ref-type="fig" rid="F4">Figure 4</xref>), although the strength of this trend varied with site and moon phase. Fish call rates at Yawzi were most influenced by time of day, particularly in the third-quarter and first-quarter moon phases (One-way ANOVA: F<sub>3,330</sub> &#x3d; 13.1, <italic>p</italic> &#x3c; 0.001, <xref ref-type="fig" rid="F5">Figure 5A</xref>; <xref ref-type="table" rid="T3">Table 3</xref>). Cocoloba also had significant differences in activity between night and dawn (Tukey&#x2019;s <italic>post hoc</italic>: <italic>p</italic> &#x3c; 0.05), and night and dusk (<italic>p</italic> &#x3c; 0.05, <xref ref-type="fig" rid="F5">Figure 5B</xref> and <xref ref-type="table" rid="T3">Table 3</xref>). For Tektite, day appeared to be the outlying period, significantly lower than dawn, dusk, and night call rates (<xref ref-type="fig" rid="F5">Figure 5C</xref>; <xref ref-type="table" rid="T3">Table 3</xref>). Interestingly, full moon was the only lunar phase in which time of day had no significant effect on activity at any site.</p>
<fig id="F4" position="float">
<label>FIGURE 4</label>
<caption>
<p>Averaged daily trends in fish call rate between three reefs. Each point is an hourly mean (2&#xa0;min of audited data, 30&#xa0;min apart), averaged across 8&#xa0;days at the same time. Mean night for study days is strongly shaded, with light shading indicating mean dusk and dawn periods.</p>
</caption>
<graphic xlink:href="frsen-05-1338586-g004.tif"/>
</fig>
<fig id="F5" position="float">
<label>FIGURE 5</label>
<caption>
<p>Effect of photoperiod and moon cycle on call rate for three reefs <bold>(A)</bold> Yawzi, <bold>(B)</bold> Cocoloba, <bold>(C)</bold> Tektite. Points and bars represent mean call rate (calls/min) and 95% confidence intervals (&#xb1;1.96&#x2a;SE) during the respective daily period, colored by lunar phase (2 days of data for each phase). Significance in call rate variation between daily light periods is shown with stars (&#x2a;<italic>p</italic> &#x3c; 0.05; &#x2a;&#x2a;<italic>p</italic> &#x3c; 0.01; &#x2a;&#x2a;&#x2a;<italic>p</italic> &#x3c; 0.001, Tukey HSD with no correction), with colored stars showing <italic>post hoc</italic> results in respective moon phase, and black representing combined significance between photoperiods.</p>
</caption>
<graphic xlink:href="frsen-05-1338586-g005.tif"/>
</fig>
<p>A single unknown call type was opportunistically identified and documented at all three reefs and plotted to compare daily call density trends between sites (<xref ref-type="fig" rid="F6">Figure 6</xref>). The call was a downswept tonal hum, ranging between 2&#xa0;Hz (average lower bound &#x3d; 82&#xa0;Hz) and 1,255&#xa0;Hz (average upper bound &#x3d; 729&#xa0;Hz) and lasting 0.2&#x2013;0.6&#xa0;s (average length &#x3d; 0.35&#xa0;s, <xref ref-type="fig" rid="F6">Figure 6B</xref>). Site-specific crepuscular peaks were observed, with dawn activity dominating at Tektite, and dusk activity dominating at Yawzi (<xref ref-type="fig" rid="F6">Figure 6A</xref>). A total of 398 of these stereotyped calls were detected, representing approximately 0.9% of the total calls identified. Similar to overall calls, the most were found at Tektite (385 calls) and the least was detected at Cocoloba (97 calls).</p>
<fig id="F6" position="float">
<label>FIGURE 6</label>
<caption>
<p>Call rates at three sites for a single, stereotyped call type. <bold>(A)</bold> Averaged hourly call rate of downswept tonal hum across 8 days, colored by site. Mean night period is strongly shaded, with mean dusk and dawn lightly shaded. Note the differences in daily patterns: a large dawn peak at Tektite, and smaller one a Yawzi, then a large dusk peak at Yawzi and smaller dusk peaks at Cocoloba. Cocoloba, the most degraded, showed the least daily variation. <bold>(B)</bold> Spectrogram of the tonal call (128&#xa0;pt, 32&#xa0;ms Hamming window, 75% overlap, 1,024&#xa0;pt FFT).</p>
</caption>
<graphic xlink:href="frsen-05-1338586-g006.tif"/>
</fig>
</sec>
<sec id="s3-3">
<title>3.3 Biodiversity indices comparison</title>
<p>The average received SPL of the audited sound files varied significantly between all sites (KW test: <italic>X</italic>
<sup>
<italic>2</italic>
</sup>(2) &#x3d; 649, <italic>p</italic> &#x3c; 0.0001, <xref ref-type="fig" rid="F7">Figure 7A</xref>), with Tektite as the site with the highest sound levels at 96.33 &#xb1; 0.27&#xa0;dB re 1&#xa0;&#xb5;Pa (mean &#xb1;1.96&#x2a;SE). Despite showing statistical significance, Yawzi and Cocoloba sound levels varied by less than a decibel, with Yawzi at 89.73 &#xb1; 0.22&#xa0;dB re 1&#xa0;&#xb5;Pa and Cocoloba slightly lower, at 89.09 &#xb1; 0.15&#xa0;dB re 1&#xa0;&#xb5;Pa (Dunn&#x2019;s test, <italic>p</italic> &#x3c; 0.005). Tektite also had the strongest crepuscular peaks in SPL (dawn-night: 5.1&#xa0;dB change, dawn-day: 1.7&#xa0;dB change, dusk-day: 0.8&#xa0;dB change, dusk-night: 4.2&#xa0;dB change), although Yawzi also saw increases during dusk and dawn versus night (dusk-night: 2.8&#xa0;dB change, dawn-night: 2.0&#xa0;dB change), although day time had the highest sound levels at this site. Cocoloba had the weakest crepuscular peaks with an average 1.2&#xa0;dB increase from night to dawn and a 1.8&#xa0;dB difference between dusk and night (<xref ref-type="fig" rid="F7">Figure 7B</xref>).</p>
<fig id="F7" position="float">
<label>FIGURE 7</label>
<caption>
<p>Averaged daily trends and distributions of acoustic indicators between reefs. <bold>(A)</bold> Recieved sound pressure level (SPL, dB re 1&#xa0;&#xb5;Pa), acoustic complexity (ACI), bioacoustic index (BIO), and entropy (H) in the low frequency band for each audited file by site. Mean and standard deviation for each site are overlayed in black. Statistical differences in distribution between sites are represented by stars (&#x2a;<italic>p</italic> &#x3c; 0.05; &#x2a;&#x2a;<italic>p</italic> &#x3c; 0.01; &#x2a;&#x2a;&#x2a;<italic>p</italic> &#x3c; 0.001, Dunn&#x2019;s test of multiple comparisons, Bonferroni adjustment). <bold>(B)</bold> Daily hourly mean values of 4 acoustic indicators averaged across 8 days, colored by site.</p>
</caption>
<graphic xlink:href="frsen-05-1338586-g007.tif"/>
</fig>
<p>In addition to SPL, several acoustic indices were tested on the same files and frequency range and compared to fish call rates. The AEI and ADI had no significant linear relationship with call rate (AEI: Multiple <italic>R</italic>
<sup>2</sup> &#x3d; 1.543e-3, <italic>p</italic> &#x3e; 0.05; ADI: Multiple <italic>R</italic>
<sup>2</sup> &#x3d; 5.297e-4, <italic>p</italic> &#x3e; 0.05) and no visible trends or differences between sites, and are thus not included in the rest of the analysis. The ACI explained less than 2% of the variation in call rates and, although weak, the linear regression was significant due to the large sample size of files (<xref ref-type="fig" rid="F8">Figure 8A</xref>, Multiple <italic>R</italic>
<sup>2</sup> &#x3d; 0.016, <italic>p</italic> &#x3c; 0.0001). The BIO was able to identify Tektite as the &#x201c;healthiest&#x201d; site, and even identified some crepuscular trends within Tektite (<xref ref-type="fig" rid="F7">Figure 7B</xref>), but was otherwise weakly related to call rate (Multiple <italic>R</italic>
<sup>2</sup> &#x3d; 0.175) and visual metrics (&#x3c4; &#x3d; 0.26). H, the product of spectral and temporal entropy, reported a negative correlation with fish calls (<xref ref-type="fig" rid="F8">Figure 8A</xref>, Multiple <italic>R</italic>
<sup>2</sup> &#x3d; 0.262, <italic>p</italic> &#x3c; 0.0001), portraying very similar, though inverted, patterns as SPL on these datasets (<xref ref-type="fig" rid="F7">Figure 7B</xref>). In addition to a strong direct relationship between SPL and H (<xref ref-type="fig" rid="F8">Figure 8B</xref>, Multiple <italic>R</italic>
<sup>2</sup> &#x3d; &#x2212;0.758), the pair had similarly strong statistical relationships with call rate (<xref ref-type="fig" rid="F8">Figure 8A</xref>) and visual metrics (<xref ref-type="fig" rid="F9">Figure 9</xref>).</p>
<fig id="F8" position="float">
<label>FIGURE 8</label>
<caption>
<p>
<bold>(A)</bold> Linear regression of call rate and acoustic indicator, colored by site. Output from each audited file is plotted, and then best fit line is overlayed in black with corresponding multiple <italic>R</italic>
<sup>2</sup> value. All regressions showed significance, with the strongest relationship with fish call rate being sound pressure level, top plot, and the weakest being the acoustic complexity index, bottom right plot. <bold>(B)</bold> Linear regression of SPL with other acoustic indicators. Top plot again shows regression between call rate and SPL, with the axes flipped. However, in this figure we can see that SPL actually has stronger relationships with both the Bioacoustic Index, bottom middle plot, and Entropy, bottom left. Similar to call rate, ACI has a negligible relationship to SPL.</p>
</caption>
<graphic xlink:href="frsen-05-1338586-g008.tif"/>
</fig>
<fig id="F9" position="float">
<label>FIGURE 9</label>
<caption>
<p>Correlation matrix between acoustic indicators derived from this study and average number of fish, fish species, and hard coral percent cover from visual surveys over 2016 and 2017 using Kendall rank correlation. Sites are delineated with colors: Cocoloba (CL) in light blue, Yawzi (YA) in red, and Tektite (TK) in purple. Kendall&#x2019;s tau (&#x3c4;) coefficient is printed for each relationship; all correlations were statistically significant and shown in red. Strong positive correlations are apparent between visual metrics and call rate and SPL, as well as a strong negative correlation with H. BIO and ACI were both weakly related to fish abundance, fish species, and hard coral cover.</p>
</caption>
<graphic xlink:href="frsen-05-1338586-g009.tif"/>
</fig>
<p>Overall, visual metrics had the strongest positive correlation with SPL (&#x3c4; &#x3d; 0.64, <italic>p</italic> &#x3c; 0.0001) and call rate (&#x3c4; &#x3d; 0.44, <italic>p</italic> &#x3c; 0.0001), and a fairly strong negative correlation with H (<xref ref-type="fig" rid="F9">Figure 9</xref>, &#x3c4; &#x3d; &#x2212;0.52, <italic>p</italic> &#x3c; 0.0001). BIO and ACI had the weakest relationships with fish abundance, fish species, and hard coral cover at these sites (BIO: &#x3c4; &#x3d; 0.26, ACI: &#x3c4; &#x3d; 0.05).</p>
</sec>
</sec>
<sec sec-type="discussion" id="s4">
<title>4 Discussion</title>
<p>With the rapid global decline of biodiversity on coral reefs, it is imperative that cost-effective methods of managing these habitats continue to be developed. Passive acoustic monitoring (PAM) has been increasingly applied to coral reef research, although how best to assess acoustic signals of biodiversity and reef state is still debated. The three sites examined in this study demonstrated clear, incremental variation in bottom substrate (e.g., coral cover), fish abundance, and fish species richness, making them ideal for exploring acoustic metrics indicative of reef community composition and quality. Manually annotated fish sounds were found to be a measure predictive of visual reef health indicators, successfully differentiating between three reefs based on fish abundance and coral cover and exposing varying levels of crepuscular spikes in activity at all the sites. Thus, this work provides a key ground-truthing foundation to support using fish calls as a means to assess coral reef health. Further, this is the first study to demonstrate that the observed differences in crepuscular activity strength in the low frequency acoustic band between reefs are the direct result of individual fish calls.</p>
<p>Tektite, the healthiest of the three reefs, with high coral cover and fish abundance, had the highest average call rate during every photoperiod and also demonstrated significant crepuscular spikes in activity, with especially low call rates during the day. Received SPL, BIO, and H were also able to distinguish Tektite as the most biologically active reef and even highlight daily trends within it, but had less success differentiating between the two less active reefs. Yawzi, the intermediate reef, had the second-highest call rates on average but the strongest variation between light periods, particularly due to low call rates at night. The degraded, algae-dominated site, Cocoloba, had the lowest call rates of the three, with weak crepuscular peaks. Similar trends can be seen with a single call type, a downswept tonal hum recorded at all three sites. The rate of this call had little daily variation at Cocoloba compared to the other healthier sites, which saw strong spikes in occurrence at either dawn (Tektite) or dusk (Yawzi). This time-of-day difference between Yawzi and Tektite is itself interesting, given that these reefs are only ca. 500&#xa0;m apart and one might assume calls would follow the same general pattern. Similar differences between nearby sites have also been noted for snapping shrimp (<xref ref-type="bibr" rid="B28">Lillis and Mooney, 2018</xref>). While this was one of the more common and stereotyped call types, it averaged less than 1 call/min at each site, a tiny fraction of the 30&#x2013;64 average calls/min recorded at the same sites. Statistically, this call type represented less than 1% of the total calls detected. Characterizing the number of unique call types at each site was beyond the scope of this study, but this single &#x201c;common&#x201d; call type certainly speaks to the diversity of low frequency sounds at these reefs.</p>
<p>Three out of the six computational methods evaluated showed some similar patterns to fish call rates (SPL, BIO, and H; <xref ref-type="fig" rid="F7">Figure 7</xref>). Averaged received SPL (dB re 1&#xa0;&#xb5;Pa) in the low frequency band, a commonly used metric for soundscapes, aligned with fish calls quite well, with Tektite having the highest levels and strongest crepuscular peaks. Dawn and dusk peaks in SPL were less apparent in the two quieter reefs, Cocoloba and Yawzi. Yawzi sound levels were significantly higher than those on Cocoloba, reflecting the reef health noted by traditional visual observations of fish and coral cover. However, the SPL differences between the two reefs were less than a decibel of difference on average and likely due to the increased daytime levels at Yawzi. This discrepancy in Yawzi&#x2019;s heightened SPL versus fish call rate during the day may have been caused by increased abiotic ambient noise during the day, a known pitfall of SPL.</p>
<p>Similarly, H identified Tektite apart from the other reefs, but differentiation between Yawzi and Cocoloba was less obvious (<xref ref-type="fig" rid="F7">Figure 7</xref>). At these sites, H had a negative relationship with all other variables and its daily trends were inverted from call rate, BIO, or SPL. Entropy is calculated from 0 to 1, with 0 being a single pure tone and 1 reflecting completely random noise (<xref ref-type="bibr" rid="B61">Seuer et al., 2008a</xref>). In terrestrial environments, for which this index was designed, it has been shown to positively correlate with the number of species (<xref ref-type="bibr" rid="B62">Seuer et al., 2008b</xref>). However, in acoustically active marine environments, dense fish choruses can drive the index down (<xref ref-type="bibr" rid="B58">Staaterman et al., 2017</xref>), which is likely what occurred here. Other aquatic studies have also observed this inverted relationship between entropy and fish activity (<xref ref-type="bibr" rid="B7">Bohnenstiehl et al., 2018</xref>) or phonic richness, a measure of the number of types of fish calls, although this relationship tends to be relatively weak (<xref ref-type="bibr" rid="B68">Williams et al., 2022</xref>).</p>
<p>BIO, which measures cumulative intensity across frequency bands (<xref ref-type="bibr" rid="B6">Boelman et al., 2007</xref>), yielded slightly weaker correlations with visual metrics and call rate at these sites. Among the few aquatic studies using BIO, one investigation revealed a significant relationship with reef state and the higher frequency shrimp patterns (<xref ref-type="bibr" rid="B68">Williams et al., 2022</xref>). Another found strong, positive correlations with planktivores and non-encrusting coral (<xref ref-type="bibr" rid="B15">Elise et al., 2019</xref>), although this was only demonstrated in one 2-h recording. Given these limited but equivocal results, BIO&#x2019;s utility (or lack thereof) could perhaps be explored further.</p>
<p>This study found that the ACI had almost no relationship with call rate or other acoustic indices and demonstrated no meaningful site or time-of-day differentiation. It was included in the analysis because of its recent proliferation in underwater soundscape literature and weak but significant correlation to call rate. However, ACI effectively gave no information about these particular reefs. This further contributes to the uncertainty around the application of ACI and acoustic indices in general to coral reef soundscapes, as they can be very case-specific and sensitive to spectral resolution and specified parameters (<xref ref-type="bibr" rid="B7">Bohnenstiehl et al., 2018</xref>; <xref ref-type="bibr" rid="B11">Dimoff et al., 2021</xref>). The contradictory literature around acoustic indices begs caution when applying them to new soundscapes without validation (<xref ref-type="bibr" rid="B38">Mooney et al., 2020</xref>). Further, the variable success of indices can lead to a pick-and-choose mentality to support the expected outcomes.</p>
<p>Manual annotation of fish calls does not come without challenges. Manual detection is time- and effort-intensive, making it unsuitable for long time-series, near-real-time monitoring, or large-scale projects. Like reefs themselves, fish sounds are highly diverse, variable, and abundant, with fish calls being largely unknown, making it challenging even for experienced acousticians. Dense, near-constant chorusing at healthy reefs almost certainly leads to missed calls during peak times, although our results suggest that counts are still representative, even with this limitation. These challenges to generalized fish call detection have also contributed to the lag in producing accurate machine-learning models to automate the process. As a terrestrial parallel, bird vocalization recognition in acoustically dense environments has advanced significantly in recent years with the rise of deep learning models, which now surpass other methods (<xref ref-type="bibr" rid="B69">Xie et al., 2023</xref>). More focused work on bringing generalized reef fish detectors up to this standard would allow fish calls to be a practical method of coral reef monitoring and could potentially avoid many of the pitfalls of acoustic proxies. This method would theoretically be applicable to low-cost, uncalibrated acoustic recorders, unlike SPL or sound exposure level (SEL), which would break down a remaining barrier of underwater PAM and allow the field to expand rapidly.</p>
<p>Addressing the question of biodiversity is a priority for aquatic researchers, especially at a time when it is quickly disappearing (<xref ref-type="bibr" rid="B13">Eddy et al., 2021</xref>). Phonic richness by manually classified call types has shown promise as a metric of reef fish diversity in other studies, but this method is also limited by time and effort allocation (<xref ref-type="bibr" rid="B25">Lamont et al., 2022b</xref>). Unsupervised clustering of fish detections, even of unknown origin, would be a critical follow-up step to tackle the question of biodiversity, but current models are limited to 3-4 larger clusters of reef sounds, rather than parsing out the extreme diversity and variability of coral reef fish calls (<xref ref-type="bibr" rid="B29">Lin et al., 2017</xref>; <xref ref-type="bibr" rid="B45">Ozanich et al., 2021</xref>; <xref ref-type="bibr" rid="B32">Mahale et al., 2023</xref>). As machine learning continues to advance, opportunities to fine-tune these methods to use total fish call variation to predict biodiversity, and particularly biodiversity changes, should be explored.</p>
<p>In conclusion, this study demonstrated the utility of individual fish calls, even of unknown identification, in characterizing reef quality&#x2013;namely, fish abundance and fish diversity, which are both known to strongly correlate with hard coral cover (<xref ref-type="bibr" rid="B73">Komyakova et al., 2013</xref>). Fish call rate analysis across 8 days differentially partitioned our three sites more accurately than any of the commonly used acoustic metrics tested, revealing spikes in crepuscular fish activity in our intermediate site that the indices missed. Our results suggest that fish calls and acoustic activity are indicators of healthy reef communities and can be applied to monitor coral reef health. Our results further add to the inconsistency and uncertainty surrounding acoustic indices in the low frequency for reef composition predictions. Manually auditing fish calls is not a proposed method for coral reef health monitoring in its current state, but rather this study was a baseline to validate it as a useful metric and encourage the development of thorough, generalized reef fish call detectors to analyze passive acoustic datasets in a meaningful time frame.</p>
</sec>
</body>
<back>
<sec sec-type="data-availability" id="s5">
<title>Data availability statement</title>
<p>The raw data supporting the conclusion of this article will be made available by the authors, without undue reservation.</p>
</sec>
<sec id="s6">
<title>Author contributions</title>
<p>SJ: Conceptualization, Data curation, Formal Analysis, Investigation, Methodology, Visualization, Writing&#x2013;original draft. NF: Data curation, Formal Analysis, Writing&#x2013;review and editing. SF: Data curation, Formal Analysis, Methodology, Writing&#x2013;review and editing. FJ: Methodology, Software, Writing&#x2013;review and editing. AA: Project administration, Writing&#x2013;review and editing. TAM: Conceptualization, Funding acquisition, Project administration, Resources, Supervision, Writing&#x2013;review and editing.</p>
</sec>
<sec sec-type="funding-information" id="s7">
<title>Funding</title>
<p>The author(s) declare financial support was received for the research, authorship, and/or publication of this article. This research was funded by National Science Foundation OCE, OTIC, and NRI awards (1806478, 2024077, 2155093, 2133029).</p>
</sec>
<ack>
<p>The experiments were conducted under National Park Service Scientific Research and Collecting Permits VIIS-2016-SCI-0017&#x2013;20 and we thank the Park staff for their support. We also thank Matthew Long and Cynthia Becker and other contributors for their assistance in the field, and the staff volunteers at Marine Research Program, University of the Virgin Islands, and the Virgin Islands Environmental Resource Station (VIERS) for their logistical assistance and support.</p>
</ack>
<sec sec-type="COI-statement" id="s8">
<title>Conflict of interest</title>
<p>The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.</p>
</sec>
<sec sec-type="disclaimer" id="s9">
<title>Publisher&#x2019;s note</title>
<p>All claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. Any product that may be evaluated in this article, or claim that may be made by its manufacturer, is not guaranteed or endorsed by the publisher.</p>
</sec>
<sec id="s10">
<title>Supplementary material</title>
<p>The Supplementary Material for this article can be found online at: <ext-link ext-link-type="uri" xlink:href="https://www.frontiersin.org/articles/10.3389/frsen.2024.1338586/full#supplementary-material">https://www.frontiersin.org/articles/10.3389/frsen.2024.1338586/full&#x23;supplementary-material</ext-link>
</p>
<supplementary-material xlink:href="DataSheet1.pdf" id="SM1" mimetype="application/pdf" xmlns:xlink="http://www.w3.org/1999/xlink"/>
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