Community Bioacoustics: Studying Acoustic Community Structure for Ecological and Conservation Insights

Chhaya, Vaibhav; Lahiri, Sutirtha; Jagan, M. Abhinava; Mohan, Ram; Pathaw, Nafisa A.; Krishnan, Anand

doi:10.3389/fevo.2021.706445

REVIEW article

Front. Ecol. Evol., 30 July 2021

Sec. Behavioral and Evolutionary Ecology

Volume 9 - 2021 | https://doi.org/10.3389/fevo.2021.706445

This article is part of the Research Topic What Sensory Ecology Might Learn From Landscape Ecology? View all 13 articles

Community Bioacoustics: Studying Acoustic Community Structure for Ecological and Conservation Insights

$\r\nVaibhav Chhaya&#x;$ Vaibhav Chhaya^†

Sutirtha Lahiri^†

M. Abhinava Jagan

Ram Mohan

Nafisa A. Pathaw

Anand Krishnan^*

Department of Biology, Indian Institute of Science Education and Research (IISER), Pune, India

The diversity of animal acoustic signals has evolved due to multiple ecological processes, both biotic and abiotic. At the level of communities of signaling animals, these processes may lead to diverse outcomes, including partitioning of acoustic signals along multiple axes (divergent signal parameters, signaling locations, and timing). Acoustic data provides information on the organization, diversity and dynamics of an acoustic community, and thus enables study of ecological change and turnover in a non-intrusive way. In this review, we lay out how community bioacoustics (the study of acoustic community structure and dynamics), has value in ecological monitoring and conservation of diverse landscapes and taxa. First, we review the concepts of signal space, signal partitioning and their effects on the structure of acoustic communities. Next, we highlight how spatiotemporal ecological change is reflected in acoustic community structure, and the potential this presents in monitoring and conservation. As passive acoustic monitoring gains popularity worldwide, we propose that the analytical framework of community bioacoustics has promise in studying the response of entire suites of species (from insects to large whales) to rapid anthropogenic change.

Introduction

With the ongoing global crisis of biodiversity loss, passive acoustic monitoring has gained popularity in both aquatic and terrestrial environments (Magurran et al., 2010; Blumstein et al., 2011; Parks et al., 2014; Linke et al., 2018; Sugai et al., 2019b), employing sound to monitor wildlife. Animal sounds are diverse and varied, and play a critical role in advertising territories and attracting mates (Marler and Slabbekoorn, 2004; Bradbury and Vehrencamp, 2011), as well as echolocation in some species (Griffin, 1958). Acoustic signal parameters and signaling strategies are influenced by noise from biotic and abiotic sources, structural features of the environment (Morton, 1975; Marten and Marler, 1977; Wiley and Richards, 1978; Wiley, 1991; Aubin and Jouventin, 1998; Nemeth et al., 2002; Blumenrath and Dabelsteen, 2004; Brumm and Slabbekoorn, 2005; Bee and Micheyl, 2008; Brumm and Naguib, 2009; Ruppé et al., 2015; Templeton et al., 2016), and the morphological constraints imposed by emitter geometry (Podos, 2001; Riede et al., 2006; Kounitsky et al., 2015). In order to compare signal parameters of different species, Nelson and Marler (1990) articulated the concept of “signal space,” where signal parameters could be quantitatively represented. Multiple factors, both evolutionary and contemporary, may influence how signals are distributed in signal space. For example, acoustic competition (i.e., competition between signalers to communicate without interference) is predicted to lead to divergence in signal parameters of coexisting species, particularly those that are closely related, such that each species in an assemblage occupies a unique region in signal space [birds: (Planqué and Slabbekoorn, 2008; Luther, 2009; Krishnan and Tamma, 2016; Krishnan, 2019a; Chitnis et al., 2020), anurans: (Littlejohn, 1959; Duellman and Pyles, 1983; Chek et al., 2003), insects: (Schmidt et al., 2013; Jain et al., 2014)]. In a scenario where competition drives signal evolution, sympatric species may also signal at different times [birds:(Ficken et al., 1974; Fleischer et al., 1985; Popp et al., 1985; Brumm, 2006; Luther, 2008; Planqué and Slabbekoorn, 2008), anurans: (Sugai et al., 2021b), fish: (Ruppé et al., 2015)] or locations in space [birds: (Nemeth et al., 2002; Chitnis et al., 2020), anurans: (Hodl, 1977), insects: (Diwakar and Balakrishnan, 2007; Jain and Balakrishnan, 2012), bats: (Kennedy et al., 2014)]. The distributions of species in signal space represent a “signature” of each community, a definitive pattern that can be monitored to track ecological changes. These “acoustic communities” represent the sum of all sound-producing species in an aquatic or terrestrial landscape (Drewry and Rand, 1983; Duellman and Pyles, 1983; Luther, 2009; Sueur and Farina, 2015; Farina and James, 2016). Community bioacoustics integrates the signal space of an acoustic community with information on species composition, diversity and signaling activity to study spatiotemporal community dynamics (i.e., seasonal and spatial variation in species composition or phylogenetic diversity) (Luther, 2008, 2009; Krishnan, 2019a; Lahiri et al., 2021). The term “acoustic community structure” (Table 1) adapts the concept of ecological community structure, employing acoustic parameters and signaling activity as measurable traits to examine the distribution of sound-producing species in signal space, together with measures of species composition and phylogenetic diversity. The wealth of data generated by passive acoustic monitoring efforts promises valuable ecological insight, both into the distributions and movements of individual species as well as community-level processes such as seasonal turnover.

TABLE 1

Table 1. Definitions and discussion of important terms related to community bioacoustics.

Here, we discuss how ecological processes drive acoustic community structure, and propose using acoustic communities to track ecological change. This serves to facilitate non-invasive biodiversity monitoring and conservation informed by behavior, ecology and natural history. The ubiquity and diversity of animal acoustic signals renders them promising indicators of ecosystem health (Sueur and Farina, 2015; Sugai et al., 2019b). Most conservation-oriented studies using passive acoustics typically use either single-species monitoring, or index-driven approaches. We suggest that biodiversity monitoring programs incorporate information on acoustic community composition and spatiotemporal dynamics (Desjonquères et al., 2018; Gasc et al., 2018; Krishnan, 2019a) to effectively and rapidly study species distributions and community turnover. This serves both as an additional use of passive acoustic data, as well as an alternative to other approaches in the field, depending on the needs of conservation. Community bioacoustics is thus potentially valuable to ecologists and conservation biologists working across scales from individual species to entire ecosystems.

Conceptual Foundations

Before examining how acoustic communities inform ecological studies, it is important to understand how ecological processes drive patterns in acoustic community structure (Krishnan and Tamma, 2016; Sugai et al., 2021a). To illustrate this concept, we use some examples from some of the main hypotheses in the field. For effective communication, a high signal-to-noise ratio ensures improved detection by the receiver, thus benefiting the signaler (Endler, 1992; Wollerman and Wiley, 2002; Hart et al., 2015; Vélez et al., 2017). However, signal efficacy is reduced by masking interference from competing sound sources, such as other nearby signalers (Schwartz and Wells, 1983; Narins, 1992; Greenfield, 1994; Aubin and Jouventin, 1998; Bee and Micheyl, 2008; Balakrishnan et al., 2014). Divergence of signal properties reduces masking, enables segregation of competing sound streams (MacDougall-Shackleton et al., 1998; Krishnan, 2019b), and thus reinforces species recognition and premating isolation between close relatives (Nelson, 1988, 1989; Grant and Grant, 1996; Qvarnström et al., 2006). In diverse animals [crickets: (Schmidt et al., 2013), cicadas: (Shieh et al., 2015), aquatic insects: (Gottesman et al., 2020), fish: (Ruppé et al., 2015; Bertucci et al., 2020), anurans: (Drewry and Rand, 1983; Duellman and Pyles, 1983; Narins, 1995; Chek et al., 2003), birds: (Kirschel et al., 2009b, 2020; Krishnan and Tamma, 2016; Chitnis et al., 2020), bats: (Heller and von Helversen, 1989; Kingston et al., 2000; Luo et al., 2019), primates: (Braune et al., 2008)], closely related sympatric species exhibit divergent signals, partitioning the acoustic resource to minimize acoustic competition. Each species is therefore predicted to occupy a unique region or “niche” in the acoustic resource, a hypothesis extrapolated from ecological niche theory (Hutchinson, 1957; Holt, 2009). This realized “acoustic niche” (Farina et al., 2011; Pijanowski et al., 2011b), in the truest sense also includes partitioning at the level of receiver perception (Luther, 2008; Lemmon, 2009; Seddon and Tobias, 2010; Amezquita et al., 2011) and measurement of signal propagation distance (Marten and Marler, 1977; Nemeth et al., 2002). The presence of unintended recipients may alter signaling behavior (Ryan et al., 1982; Zuk et al., 2006). All of these factors influence the volume over which the signal elicits a response, or its “active space” (Brenowitz, 1982; Lohr et al., 2003; Bradbury and Vehrencamp, 2011), and are thus important in measuring overall signal discriminability. However, it is not always possible to investigate receiver partitioning in the field, and most studies of signal partitioning are, therefore, concerned with divergence at the level of signal parameters and the spatiotemporal distribution of signalers.

Competition, however, is not the only factor influencing signal evolution, and thus acoustic traits within communities of species. For example, habitat constraints on sound transmission are predicted to drive signal convergence toward parameters optimal for transmission in a certain habitat (the acoustic adaptation hypothesis, where acoustic signals adapt toward maximized transmission in a particular habitat) (Morton, 1975; Marten and Marler, 1977; Wiley, 1991; Snell-Rood, 2012). In bats, where time-frequency parameters of echolocation pulses have a significant effect on perception and navigation, species occupying the same habitat may possess convergent signals (Parsons and Jones, 2000; Jones and Holderied, 2007). Other vocalizations may also converge owing to conserved function, including alarm calls that are critical for survival (Marler and Slabbekoorn, 2004; Braune et al., 2008). Acoustic adaptation remains debated in the field (Ey and Fischer, 2009), and more studies are necessary to elucidate how ecological processes drive acoustic signal evolution. Patterns of divergence or convergence of signals may also be driven by other factors. For example, sexual selection may drive signal divergence by female choice (Seddon et al., 2013), whereas communication between competing species (extended communication networks) may drive signal convergence (Tobias et al., 2014). Alternatively, neutral processes may drive entirely different patterns in signal evolution, such as signals resembling each other on account of phylogenetic relatedness (Wilkins et al., 2013). Thus, although we discuss patterns of divergence or convergence as examples to illustrate our analytical framework, we note that the drivers of these patterns are diverse. Regardless of this, the patterns in acoustic community structure may themselves provide valuable information, and we use the examples discussed above to illustrate the utility of this approach.

A Framework to Quantify Acoustic Community Structure

The first step in understanding acoustic community structure is to quantify the acoustic traits of all species in a community. The concept of signal space provides a means to quantitatively interrogate whether the signals of coexisting species overlap. Broadly, signal space encompasses spectral and temporal properties of a sound (Figure 1), by quantifying parameters of a vocal unit, for example, a note (parameters include peak frequency and note duration, to name a few) and representing them as a point in multidimensional space. The entire repertoire forms a cloud of such points, the volume of which represents each species’ signal space (Nelson and Marler, 1990), which is constrained both by physical characteristics and the transmissibility of sound (Wilkins et al., 2013). Signal space of diverse sensory signals can be examined at scales ranging from individual species to entire communities or lineages, analogous to a functional trait space in community ecology (Endler, 1992; Stoddard and Prum, 2008; Luther, 2009; Krishnan, 2019a; Chitnis et al., 2020; Krishnan et al., 2020; Lahiri et al., 2021). As an outcome of diverse ecological processes, an acoustic community exhibits organization within signal space. Using the tools of community ecology and community phylogenetics, we may obtain a series of metrics that quantitatively represent the acoustic community, and we lay these out below.

FIGURE 1

Figure 1. Signal space (top right), derived using principal components analysis on acoustic signal parameters of diverse species (A–F, top left) enables study of acoustic communities across spatiotemporal scales, including different seasons (color codes). Signal space for each species is represented as the volume occupied by the entire repertoire (larger circles, with the smaller point representing the centroid). Bottom panels: Acoustic community structure varies along both spatial and temporal axes (color codes represent different seasons). This figure loosely depicts some bird species from an acoustic community in western India for illustrative purposes, demonstrating seasonal turnover, with species replacing each other, and spatial segregation, with each species singing from a preferred location in space (Krishnan, 2019a).

At the outset, it is important to quantify species diversity and signal space of any acoustic community. For the first, a census of species detected in an acoustic dataset, together with measures of how frequently their vocalizations are detected, provides an estimate of community diversity. In order to quantify community signal space, a call library consisting of the signals of each species is digitized to extract signal parameters (Luther, 2009; Krishnan, 2019a; Lahiri et al., 2021), which are then ordinated using multivariate methods such as principal components or linear discriminant analysis. Thus, all sounds in a community are represented as points in signal space. Ideally, the digitized signals should represent intra- and interspecific variability in signals within the population under consideration, and may be obtained either directly from passive recordings or by making focal recordings to build a call library before passive sampling. The latter is more reliable in poorly studied areas, as it enables researchers to match vocalizations to species before passive sampling.

Signal partitioning is an example of a process which is predicted to lead to overdispersion, where points representing the different acoustic signals are further apart than expected by chance (Chek et al., 2003). The converse is true in case of signal convergence, where clustering around a central tendency is predicted. Clustering may also arise due to phylogenetic relatedness of coexisting species, as the signals of close relatives are likely to resemble each other (i.e., they are phylogenetically conserved) (Figure 2), and quantifying the phylogenetic signal in acoustic traits provides a way to test these hypotheses. Studies have uncovered significant overdispersion in some bird acoustic communities (Luther, 2009; Krishnan, 2019a; Chitnis et al., 2020). These studies hypothesize that acoustic competition may drive the structure of the acoustic community by divergence of time-frequency parameters. Other studies, however, suggest that environmental filtering (for example, acoustic adaptation to habitat features) may result in community convergence instead (Planqué and Slabbekoorn, 2008; Cardoso and Price, 2010). These examples illustrate how the various drivers of signal evolution may lead to distinct patterns in the signal space of a community.

FIGURE 2

Figure 2. Community phylogenetic analyses and signal space. Phylogenetic information is an important component in our understanding of acoustic community assembly and structure. In a hypothetical, simplified series of communities drawn from the phylogeny on the left [inspired by the principles of community phylogenetics (Webb, 2000; Cavender-Bares et al., 2004)], phylogenetic overdispersion or clustering combined with similar patterns in signal space suggest that phylogenetic relationships drive acoustic community structure (top left and bottom right squares), whereas other patterns may be driven by signal partitioning or convergence, among other processes (top right and bottom left).

In order to statistically examine overdispersion versus convergence in signal space, studies typically employ null model tests (Chek et al., 2003; Chitnis et al., 2020; Sugai et al., 2021a). Null model tests in community ecology compare observed interspecific trait differences or co-occurrence patterns to those in randomly distributed “null” communities (Harvey et al., 1983; Gotelli, 2000; Gotelli and Entsminger, 2001; Gotelli and McCabe, 2002). These tests thus inform us whether species are more likely to co-occur, or certain community trait values are more likely to exist than expected by chance. When studying acoustic communities, null model tests are employed to detect whether species are further apart or closer in signal space than expected by chance (Chek et al., 2003). Interspecific distances greater than those in the null communities are consistent with overdispersion, or signal divergence, whereas clustering is consistent with signal convergence or phylogenetic conservatism (Planqué and Slabbekoorn, 2008; Cardoso and Price, 2010; Schmidt et al., 2013; Tobias et al., 2014).

With detailed phylogenetic information now available for many taxa that produce acoustic signals (Jetz et al., 2012; Shi and Rabosky, 2015), the tools of community phylogenetic analysis (Webb, 2000; Cavender-Bares et al., 2004; Kembel et al., 2010) help us test hypotheses about the role of processes such as competition or environmental filtering in driving the distribution of points in signal space (Figure 2). These methods combine quantification of community phylogenetic structure and diversity with trait space patterns to understand community assembly and organization. For example, overdispersion in signal space coupled with phylogenetic clustering is a pattern consistent with signals of close relatives within a community diverging, potentially to minimize competitive overlap. Conversely, phylogenetic overdispersion coupled with clustering in signal space is consistent with the hypothesis of community convergence. Measures of community phylogenetic dissimilarity and beta-diversity (Ives and Helmus, 2010) may also be used to quantify species turnover in acoustic communities. Although care should be applied when interpreting patterns in community phylogenetics (Gerhold et al., 2015), these analyses provide a preliminary understanding of the relationship between phylogenetic structure and signal space (Lahiri et al., 2021). Additionally, by comparing phylogenetic community structure to different trait spaces, we may investigate the contribution of indirect effects (such as morphological divergence) to acoustic community structure (Krishnan and Tamma, 2016). These indirect effects may be important, particularly in light of the relationship between morphological characters and acoustic traits. Phylogenetic analysis thus opens up important avenues in community bioacoustics, and when combined with trait data, provides insight into the organization and turnover of acoustic communities.

Spatial and Temporal Dimensions of the Acoustic Community

Divergent signal parameters represent only one aspect of acoustic signal partitioning. In addition, many organisms also signal at different times (temporal partitioning, distinct from the temporal properties of the notes themselves, which are used to calculate signal space) or locations in space (spatial partitioning). Temporal partitioning may involve fine-scale adjustments to signal timing and repetition rate, resulting in interdigitation of the signals of different individuals [birds: (Cody and Brown, 1969; Ficken et al., 1974; Fleischer et al., 1985; Popp et al., 1985; Brumm, 2006)]. Alternatively, both terrestrial and aquatic species may simply signal at different times of the day from each other, or even in different seasons [birds: (Luther, 2008; Krishnan, 2019a), bats: (Adams and Thibault, 2006; Mancina et al., 2012), fish: (Ruppé et al., 2015; Bertucci et al., 2020), marine mammals: (De Vreese et al., 2018)]. Further research is required to understand if diel-scale temporal partitioning results indirectly from ecological separation in foraging time, or by adjustments to the presence of competing signalers. Spatial partitioning, on the other hand, involves divergence in the locations from which the signal is emitted (Hodl, 1977; Bee, 2008). Segregation in space or stratification of singing heights have been documented in diverse taxa [insects: (Diwakar and Balakrishnan, 2007; Jain and Balakrishnan, 2012), birds: (Nemeth et al., 2002; Chitnis et al., 2020), bats: (Kalko and Handley, 2001; Kennedy et al., 2014)]. This pattern is putatively linked to maximizing sound transmission at a particular location (Miller and Degn, 1981; Dabelsteen et al., 1993; Nemeth et al., 2002; Marler and Slabbekoorn, 2004; Mathevon et al., 2005; Barker and Mennill, 2009; Kirschel et al., 2009a; Sprau et al., 2012; Núñez et al., 2019), or to indirect partitioning as a result of other ecological processes (Jain and Balakrishnan, 2012; Kennedy et al., 2014; Chitnis et al., 2020). For example, competition for resources may also drive signal partitioning as a by-product (Aldridge and Rautenbach, 1987; Norberg and Rayner, 1987; Kingston et al., 2000; Kingston and Rossiter, 2004; Siemers and Schnitzler, 2004; Kirschel et al., 2009b; Mancina et al., 2012; Krishnan and Tamma, 2016; Roemer et al., 2019). On the other hand, acoustic adaptation is hypothesized to lead to convergence, where species with similar signals occupy similar regions in physical space to maximize sound transmission (Boncoraglio and Saino, 2007). Patterns such as these highlight how distinct ecological processes may both directly and indirectly (Wilkins et al., 2013) drive signal partitioning, and thus acoustic community structure, along multiple axes. These axes range from signal parameters (and thus distributions of species in signal space) to the spatial and temporal distribution of signaling species.

Finally, the radiation and propagation patterns of emitted sound are an oft-ignored aspect of signal partitioning. Radiation patterns are shaped dynamically by the morphology of the sender aperture (Feng et al., 2012; Kounitsky et al., 2015), and emitted sounds are directed by the aim of the head (Ghose and Moss, 2003). Directionality of the signal impacts the perceived amplitude (Naguib, 1995), and aiming competing signals away from each other may further reduce interference, enabling signalers to avoid overlap in their active spaces. Signal amplitude is highly consequential for signal perception and attention (Dantzker et al., 1999; Greenfield and Rand, 2000; Brumm and Todt, 2003; Patricelli et al., 2007; Yorzinski and Patricelli, 2010), and for targeting biosonar in bats (Surlykke et al., 2012; Jakobsen et al., 2013). However, relatively few studies have quantified signal directionality and aiming in the field. This is in part because one requires an array of calibrated microphones, as well as estimates of distance from the source, head aim, horizontal and vertical angles to measure sound directionality accurately in the field (Blumstein et al., 2011). By quantifying signal directionality, the principles of engineering acoustics are directly applied in ecological studies to, for example, understand whether behavioral changes (such as aiming of signals in different directions) reduce the overlap of competing signals in certain environments. In addition, the use of multiple microphones to study these patterns may also prove useful in estimating the relative numbers of different signaling species using triangulation (Blumstein et al., 2011; Mennill et al., 2012). Although sound propagation patterns may differ in aquatic environments, similar general principles and techniques may be used to quantify both signal partitioning (Ruppé et al., 2015; Bertucci et al., 2020) and acoustic community structure (Hannay et al., 2013; De Vreese et al., 2018; Desiderà et al., 2019; Mooney et al., 2020). Using community structure and composition, including the distributions of species in signal space, we may obtain valuable ecological and conservation insight from non-invasive acoustic data, and we explore these possibilities in the sections below.

Acoustic Community Structure as a Barometer of Ecological Change

The patterns and processes discussed above imply that each acoustic community is likely to possess a distinct structure, driven both by the diversity of signals (and their distributions in signal space) as well as the spatial and temporal distributions of signaling species. Because communities are not static, ecological changes (spatial and temporal) are likely to be reflected in acoustic community structure, and we may thus use this framework to quantify and detect these changes. For example, seasonal changes such as hibernation or migration may alter the composition and phylogenetic diversity of both terrestrial and marine acoustic communities (Hannay et al., 2013; Putland et al., 2017; De Vreese et al., 2018; Krishnan, 2019a). Additionally, acoustic communities may exhibit small and large-scale spatial heterogeneity, because habitat preferences of signaling species drive differences in distribution (Van Parijs et al., 2001; Figure 3). Quantifying signal space helps us understand seasonal dynamics and habitat occupancy of acoustic communities, providing real-time information on species distributions and movements. This data potentially enables us to detect arrivals and departures both along migration routes and wintering grounds by measuring turnover in the acoustic community. Further studies could then use multi-year acoustic data to quantify the effects of extensive urbanization or shipping traffic on the migration and community structure of birds, bats and marine mammals. Human impacts are predicted to profoundly affect migrant numbers and timing of arrival, and community bioacoustics provides an early warning of these changes for terrestrial and aquatic ecosystems (Sanders and Mennill, 2014). Studies have quantified phenology (Buxton et al., 2016), or seasonal ecological patterns in bird communities over large geographical areas. Many studies of this variety utilize ecoacoustic or soundscape indices to quantify broad changes in sound profiles (Villanueva-Rivera et al., 2011; Sueur and Farina, 2015). Indices typically either quantify attributes of a recording, or compare recordings to each other in a manner similar to quantifying beta-diversity (Villanueva-Rivera et al., 2011; Desjonquères et al., 2020). Although useful for rapid assessments, they do not provide species-level information, and may sometimes provide conflicting results with census methodologies (Lellouch et al., 2014; Krishnan, 2019a). Thus, studies operating at multiple scales should combine the use of ecoacoustic indices with more detailed analyses of the kind we propose here. The quantification and utility of soundscape indices has been covered in multiple reviews and publications (Farina et al., 2011; Pijanowski et al., 2011a, b; Sueur and Farina, 2015; Gasc et al., 2017; Buxton et al., 2018a, b; Gibb et al., 2019), and the two approaches are compared and contrasted in Table 2. Thus, although our review focuses more on the use of acoustics to study community ecology and change, using the acoustic community as a unit, a combination of different approaches may prove fruitful for future studies.

FIGURE 3

Figure 3. Ecological changes are reflected in the acoustic community. Spatiotemporal change in a hypothetical bat acoustic community (consisting of resident and migrant species). Each habitat within this landscape is represented by a square, with colors representing different habitat types. Each bat species calls at a distinct frequency (see key on the left), and species composition in each cell changes with seasonal transitions (top row). Recorders placed in each square are predicted to detect spatiotemporal changes in acoustic community structure (bottom row), serving as a framework for long-term monitoring. Similar changes may also occur due to hibernation or seasonal differences in signaling activity.

TABLE 2

Table 2. Comparison of the information provided by quantifying acoustic community structure using census methodology versus quantifying acoustic diversity using ecoacoustic indices.

For instance, by combining indices with census of changes in species composition, together with change in the community signal space, we can detect the effects of migration on community structure (Krishnan, 2019a). The strength of community bioacoustics lies in providing detailed single-species information as well as data on overall community diversity (Table 2). Gathering these data across seasons or multiple years provides a non-invasive way to track temporal community change. In addition to migration, many bat species enter hibernation in inclement weather, resulting in their absence from the acoustic community. Hibernating bats are very sensitive to environmental changes (Fenton, 2012; Nocera et al., 2019). Long-term community acoustic data potentially provides information on whether individual species are declining, on changes to hibernation timings, and changes in overall community diversity over time.

Heterogeneity in habitat and species distributions across a landscape is also putatively reflected in a corresponding heterogeneity of acoustic communities (Luther, 2009). Acoustic monitoring has proved very useful in understanding occupancy of species which are hard to detect using traditional survey methods (Weller and Baldwin, 2012; Kalan et al., 2015; Campos-Cerqueira and Aide, 2016; Law et al., 2018; Gibb et al., 2019; Abrahams and Geary, 2020), and this provides a starting point to quantify spatial structure in the acoustic community. Occupancy, or the proportion of sites occupied by a species of interest, provides a quantitative estimate of the distribution and spread of a species. Dynamic multispecies occupancy models enable quantitative description of spatial heterogeneity in the acoustic community, as well as detection of the effects of environmental change on the relative distributions of species (Dorazio et al., 2010; Iknayan and Beissinger, 2018). There is a need for more large-scale multispecies occupancy studies using acoustics, in order to comprehensively quantify spatial community structure. This, together with metrics of community beta-diversity (Avolio et al., 2019), enables site-by-site spatial diversity comparisons. We may then test two contrasting hypotheses: does signal similarity drive spatial segregation in species distributions, or does habitat structure indirectly structure the acoustic community (Sugai et al., 2021a)? Similar analyses have also proved useful in understanding how isolation on islands influences the acoustic community, and thus signal partitioning in birds (Robert et al., 2019). This study framework therefore has great value in understanding the relationship between biogeography and acoustic community structure. Combining data from multiple recorders with triangulation algorithms will enable estimates of density and relative numbers of each signaling species in the community, and even open up the possibility of tracking local movements of taxa such as marine mammals (Blumstein et al., 2011).

Current Limitations in Community Bioacoustics, and Possible Solutions

In spite of the usefulness of community bioacoustics, certain limitations must be considered as areas for future streamlining and improvement. Firstly, scientific studies undertaking biodiversity inventories including passive acoustics should be mindful of taxa that are silent or infrequently vocal, and use a combination of survey methods to detect all species (Darras et al., 2018; Wheeldon et al., 2019). For example, relatively silent birds such as storks, or fruit bats that do not produce echolocation calls, may be more reliably detected by visual surveys. Thus, the acoustic community is best treated as a surrogate of the ecological community, and as an indicator of its diversity rather than an exact inventory. Secondly, censusing massive acoustic data to quantify community structure can be labor-intensive. Recent advances in automated species recognition provide hope of a streamlined analytical pipeline (Mac Aodha et al., 2018; Ulloa et al., 2018; Stowell et al., 2019). However, in understudied tropical regions, comprehensive call libraries are a relatively recent phenomenon, and there is a global paucity of information on many taxa (Chakravarty et al., 2020; Desjonquères et al., 2020). More data is needed to improve automated recognition, particularly in high-noise environments where the sounds from multiple vocal species may result in masking that interferes with many recognition algorithms. In the meantime, researchers in these regions should consider randomized subsampling of large datasets, (Krishnan, 2019a) which may provide a more tractable method to census the acoustic community. This approach will also reduce the computational power required.

Another issue generally faced by passive acoustic studies is correcting for detectability in estimates of occupancy and community composition (Darras et al., 2016). This is particularly relevant for bats and dolphins, whose ultrasonic signals attenuate quickly over distance in a frequency-dependent manner. Low signal-to-noise ratios further accentuate this problem, reducing detectability of calls (Sugai et al., 2019a). Thus, false absences of higher-frequency species must be accounted for in any study, potentially by correcting the data to account for differences in detectability (Meyer et al., 2011) or by matching visual and acoustic survey data (Richman et al., 2014). Playback experiments using speakers may provide a detection space for each species in an environment, which can then be implemented in an occupancy-based model. Combining this method with triangulation, as described earlier, may help refine estimates and even provide relative abundance data for each species in a community (Mennill et al., 2012). This is an important area of future research into expanding the possibilities of acoustic monitoring.

Synthesis: Community Bioacoustics in Long-Term Biodiversity Monitoring and Conservation

As the Anthropocene brings with it rapid changes in the earth’s biodiversity, long-term biodiversity monitoring is the need of the hour to inform policy and conservation (Magurran et al., 2010). Non-invasive monitoring methods, in particular, are powerful sources of continuous ecological data. For this reason, passive acoustic monitoring has increased in popularity both in marine and terrestrial environments. Human activities such as land-use change could fundamentally alter spatiotemporal acoustic community structure (Zuk et al., 2006; Gasc et al., 2018; Torrent et al., 2018; Pillay et al., 2019), at the extreme resulting in the loss of natural sounds (Pijanowski et al., 2011a; Sueur et al., 2019). Quantifying these effects is very important in developing conservation policy for diverse ecosystems, from forests and deserts to the ocean depths. Studying how anthropogenic change influences spatiotemporal community composition could inform conservation planning and management, by serving both as an early warning system and as a barometer of the extent of ecological change.

As recorders become increasingly cost-effective (Hill et al., 2019), the potential for acoustic monitoring, particularly in tropical countries that harbor most of the world’s biodiversity, is tremendous (Wrege et al., 2017). With these developments comes a need for capacity-building not just in the collection of data, but also in building robust analytical frameworks that support science and conservation planning. As a highly biodiverse tropical country, the example of India serves to illustrate the global promise of community bioacoustics, and the need for more studies utilizing these methods. There are still relatively few passive acoustic studies in India (Diwakar et al., 2007; Buxton et al., 2018a; Krishnan, 2019a; Lahiri et al., 2021), and most acoustic sampling relies on call counts or focal recordings (Khaling et al., 1998; Ghose et al., 2003; Agnihotri et al., 2014; Purushotham and Robin, 2016). For lesser-known Indian taxa such as bats, comprehensive call libraries are few (Raghuram et al., 2014; Wordley et al., 2018; Chakravarty et al., 2020). Expanding the study of acoustic community structure will thus be extremely valuable in understanding and conserving global biodiversity. The ability to rapidly collect large amounts of data in the absence of observers sets passive acoustics apart from focal community sampling (Haselmayer and Quinn, 2000; Abrahams, 2019). Even when deploying passive recorders for single-species surveys, a wealth of community-level information may be obtained. Most studies we have illustrated in this review, however, focus largely either on single species, or use indices for broader comparisons. By studying acoustic community dynamics, deriving a community signal space based on acoustic parameters, and quantifying the diversity of communities in different habitats, we can build a comprehensive tapestry of signaling species across landscapes. This enables us to obtain information both on individual species, as well as entire communities, using the same datasets as other passive acoustic studies. For example, by recording the acoustic community, we may identify the habitat preferences of each individual species (as detailed above), compare different sites to measure differences in community composition and diversity across different habitat types, and also track change in the overall community (and individual species) over time. Therefore, if anthropogenic activity alters the distribution of a certain species, this will be detected by passive recorders, and will also change community composition over time. By measuring the effect of anthropogenic changes on community turnover (for example, beta-diversity as a response variable), we can obtain valuable ecological information across scales.

For threatened species, acoustic community structure, diversity and dynamics at known sites is a useful barometer of ecosystem health. Studies using acoustics to date primarily focus on presence-absence of specific species, or on occupancy patterns, as detailed earlier. However, community-level data provides considerably more in the way of potential opportunities for conservation insight. For example, we can identify what species typically co-occur with a certain threatened species in the acoustic community, and the patterns of community structure in its preferred habitat. This could potentially be used to identify new priority sites for survey, reintroduction or conservation of these species, and to evaluate the success of reintroduction and restoration efforts (Lewis et al., 2021). Sites that possess the requisite suite of co-occurring species may be suitable for reintroduction of a threatened species, and community structure may be monitored after reintroduction, to measure whether it returns to a pattern similar to the source site. Such efforts are particularly relevant in insular ecosystems, where eradication of invasive species and translocation of native species is being undertaken to restore ecological communities (Borker et al., 2020). Acoustic community structure could provide a well-defined, easily quantified metric of the success of these efforts in restoring native insular communities of birds, frogs, insects, and other signaling animals.

Community bioacoustics will further enable quantification of long-term change in global ecosystems. This, in turn, will help understand how human-induced environmental changes impact global biodiversity, from densely populated cities to the ocean depths. Although approaches driven by indices are gaining popularity in passive acoustic studies, there is also great benefit in approaches that provide species-level, natural history-driven information that is of direct use in informing conservation policy. Community bioacoustics, and specifically acoustic community structure, is an approach that provides this information, from the entire community down to individual species (Krishnan, 2019a; Pillay et al., 2019). By quantifying the distributions and volume occupied by species in community signal space, together with phylogenetic diversity (Lahiri et al., 2021; Figure 4), field researchers may compare them across environmental conditions or grades of anthropogenic impact. For instance, we can compare signal spaces across different land-use types, to examine how the distributions of species within signal space change. This enables a non-invasive estimate of how land-use change impacts community diversity, phylogenetic diversity and the composition of communities of sound-producing species. The same data can also be used to track how detections of individual species change across land-use types. These comparisons thus provide critical data on acoustic community structure, which reflects the ecological impacts of anthropogenic change. By broadening the use of community bioacoustics, we can thus apply an interdisciplinary understanding of acoustic signaling to inform effective global biodiversity monitoring and conservation.

FIGURE 4

Figure 4. A generalized work flow highlighting the utility of community bioacoustics in long-term monitoring and conservation. By combining a quantification of community signal space with phylogenetic analyses and passive acoustic census of spatiotemporal community diversity, we may track ecological changes, inform conservation measures and also gauge their success over time.

Author Contributions

VC, SL, MJ, and AK contributed to figure conception and design. All authors listed made substantial, direct and intellectual contributions to the text, and approved this manuscript for publication.

Funding

AK is funded by an INSPIRE Faculty Award from the Department of Science and Technology and an Early Career Research Award (ECR/2017/001527) from the Science and Engineering Research Board (SERB), Government of India, and is a recipient of a Wildlife Acoustics Scientific Product Grant. SL is a recipient of an Oriental Bird Club Conservation Grant and equipment support from Idea Wild. RM is a recipient of a Rufford Foundation Small Grant. VC and MJ are both recipients of KVPY Fellowships from the Government of India.

Conflict of Interest

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.

Publisher’s Note

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.

Acknowledgments

We thank Shivam Chitnis and Rohit Chakravarty for comments, Ritesh Dighe and Vivek Kannadi for photographic references, and the reviewers for constructive feedback.

References

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