Common and Antarctic Minke Whales: Conservation Status and Future Research Directions
- 1Scottish Association for Marine Science, Oban, United Kingdom
- 2Bio-Waves, Inc., Encinitas, CA, United States
- 3Commonwealth Scientific and Industrial Research Organisation Land and Water, Townsville, QLD, Australia
- 4Institute for Marine Sciences, University of California, Santa Cruz, Santa Cruz, CA, United States
Minke whales comprise some of the most widely distributed species of baleen whales, some populations of which are still regularly targeted by commercial whaling. Here, we review the conservation status of common (Balaenoptera acutorostrata) and Antarctic (Balaenoptera bonaerensis) minke whale populations, against the backdrop of ongoing whaling operations and other anthropogenic threats, including climate change, entanglement in fishing gear, ship strikes, and noise pollution. Although some coastal minke whale populations have been studied in detail, others, which inhabit remote and ecologically sensitive locations, such as the Antarctic ice shelf, are among the least understood populations of marine mammals. The unresolved taxonomy of dwarf minke whales further highlights some of the existing knowledge gaps concerning these species. Due to their relatively small size and elusive behaviors, large uncertainties exist for almost all minke whale populations with respect to behavior, migratory routes and winter distributions, hindering effective conservation and management. However, recent advances in research technology, such as passive acoustic monitoring (PAM), unmanned aerial systems (UAS), multisensor recording tags, and machine learning assisted photo-identification, are increasingly being applied to study minke whales and their habitat, and are starting to open new windows into their life history and ecology. In future research, these non- and less-invasive methods should be integrated in larger-scale comparative studies aiming to better understand minke whale behavior, ecological interactions and their varying habitats to drive and support effective species conservation.
Many baleen whale populations have been reduced extensively by whaling, which makes them more vulnerable to negative impacts from changes in their habitats (Baker and Clapham, 2004). In the case of minke whales, several populations are still being impacted by ongoing commercial whaling. These hunts are carried out against the backdrop of global climate change and other anthropogenic impacts, such as interactions with fisheries, pollution, as well as ship strike. Given this complex array of often interacting threats and considering their comparatively long life spans, minke whales, like other baleen whales, face significant challenges that may lead to severe impacts on populations.
Minke whales inhabit all oceans, including tropical as well as polar waters (Figure 1). Since the late 1990s, two different species have been recognized: the common minke whale (Balaenoptera acutorostrata) and the Antarctic minke whale (Balaenoptera bonaerensis). Molecular data suggests that the two species are sister taxa and their clade is sister to the other Balaenopteridae and the gray whale (Eschrichtius robustus) (Rychel et al., 2004) but there is still some ambiguity about the phylogenetic relationships of minke whales to other species (Perrin et al., 2018). For the common minke whale three putative subspecies have been proposed; Balaenoptera acutorostrata acutorostrata in the North Atlantic, Balaenoptera acutorostrata scammoni in the North Pacific and the dwarf minke whale, unnamed subspecies, in the Southern hemisphere (Rice, 1998). Dwarf minke whales were first recognized as a distinct form of the common minke whale in the mid-1980s (Best, 1985), and genetic evidence suggests the existence of at least two different populations in the Southern Hemisphere (Pastene et al., 2010). The exact placement of the dwarf minke whales in the taxonomy of this species complex is still unclear. For example, South Atlantic dwarf minke whales are more closely related to North Atlantic common minke whales, than either are to dwarf minke whales from the South Pacific, indicating that their subspecies status needs further study (Pastene et al., 2010).
Figure 1. Range map of Common (Balaenoptera acutorostrata) and Antarctic (Balaenoptera bonaerensis) minke whales. Source for presented species ranges: International Union for Conservation of Nature (IUCN) (Cooke et al., 2018a,b).
The seasonal distribution and migration patterns of nearly all populations of minke whales are poorly understood. Their small size, inconspicuous behavior and seasonal distribution in remote pelagic and sea ice habitats contribute to this lack of understanding. Existing knowledge is often obtained from studying populations that frequent coastal habitats or based on incomplete historical whaling records. At least some proportion of the population of minke whales in the western North Atlantic appear to migrate to the Caribbean during winter (Mitchell, 1991; Risch et al., 2014a). The Gulf of St. Lawrence is a known summer feeding habitat (Lynas and Sylvestre, 1988; Doniol-Valcroze et al., 2007). In the central North Atlantic, pronounced sexual segregation exists on higher latitude feeding grounds, with females occurring further north, off western Greenland, while males remain further south and to the east of Greenland (Laidre et al., 2009). Tracks of satellite-tagged minke whales indicate a southward movement, following the mid-Atlantic ridge, as far south as at least 28°N starting in autumn (September to November) (Víkingsson and Heide-Jørgensen, 2015). During summer and early fall (June to November), minke whales in the eastern North Atlantic occur around the British Isles (Macleod et al., 2004; Tetley et al., 2008; Risch et al., 2019) and Norway (Heide-Jørgensen et al., 2001), while their winter distribution remains largely unknown. However, minke whales have been observed year-round around the Canary Islands (van Waerebeek et al., 1999), but only occasionally off Portugal, Spain and West Africa (Aguilar et al., 1983; van Waerebeek et al., 1999). The species is a relatively rare visitor in the Mediterranean basin with one sighting reported from the Black Sea (Reeves and Notarbartolo di Sciara, 2006).
In the North Pacific, minke whales are widely distributed north of 30°N, shifting their distribution northward during summer (Zerbini et al., 2006). However, they also occur year-round off central California (Dorsey et al., 1990). In the Central and Eastern Pacific, acoustic data suggest minke whale presence from approximately 15–35°N in deep waters surrounding subtropical volcanic islands and atolls during winter and spring (Rankin and Barlow, 2005; Rankin et al., 2007; Oswald et al., 2011; Norris et al., 2017). Data from Korea and Japan indicate seasonal southbound migrations in the western North Pacific, with unknown final destinations (Ohsumi, 1983).
The distribution of dwarf minke whales spans the entire southern hemisphere (Figure 1). They have been visually recorded in coastal waters of South America and South Africa in the Atlantic (Zerbini et al., 1996; Acevedo et al., 2006) and in waters off both western and eastern Australia, New Zealand, and New Caledonia in the Pacific (Dawson and Slooten, 1990; Arnold, 1997; Garrigue and Greaves, 2001; Gedamke et al., 2001). Although they are less commonly observed south of 65°S than Antarctic minke whales (Branch and Butterworth, 2001), dwarf minke whales are sympatric with Antarctic minke whales in much of their range (Acevedo et al., 2011), which renders some of the visual based information on the distribution of both species ambiguous or inaccurate, due to missing or incorrect identification to species level at sea (Cooke et al., 2018a).
Antarctic minke whales have a circumpolar distribution south of 60°S during summer (Figure 1), with high densities reported in parts of the Weddell and Ross Seas (Kasamatsu et al., 1995). The species is highly associated with sea ice and is generally less abundant in ice-free waters (Herr et al., 2019). Recent acoustic data show detections of the species in association with sea ice for most of the year (Dominello and Široviæ, 2016). However, this species has also been observed and recorded in sub-tropical waters of the South Atlantic, South Pacific, and Indian Ocean during winter (McCauley, 2004; Cerchio et al., 2018). A bi-modal temporal distribution pattern of Antarctic minke whales has been visually observed off South Africa, peaking in fall and spring, suggesting migratory movements by parts of the population to lower latitude habitats during winter (Best, 1982). There is also some evidence that Antarctic minke whales occasionally occur north of the equator (Glover et al., 2010; De Boer, 2015).
With this review, we aim to summarize current knowledge on the threats global minke whale populations are facing, review current research and monitoring approaches and discuss data gaps and future research and conservation priorities.
Antarctic minke whales provide a good example of a baleen whale species that are at risk from multiple environmental pressures driven by climate change. The marine ecosystem around the Antarctic Peninsula is experiencing dramatic warming (Morris and Vaughan, 2003) and significant reductions in the extent and duration of seasonal sea ice cover (Stammerjohn et al., 2008, 2011, 2012). These changes affect every component of the ecosystem (Schofield et al., 2010; Ducklow et al., 2012), but particularly the demography, behaviors and ecology of predators that rely on sea ice for foraging habitat and prey, such as Antarctic krill (Euphausia superba). The life history and population dynamics of krill are heavily influenced by climate forcing (Nicol, 2006), so predators of krill must respond to inter-annual variability in prey availability and alter their behavior and demography in response to such changes (e.g., penguins and seals; Fraser et al., 1992; Reid and Croxall, 2001; Fraser and Hofmann, 2003; Reid et al., 2005). Currently we do not understand how large-scale changes in climate and sea ice cover will affect these ecological relationships, because the linkages between these predators and their prey remain poorly studied (Fraser and Hofmann, 2003).
Antarctic minke whales are the largest ice-dependent krill predators in the Southern Ocean. As their distribution and ecology are directly tied to sea ice (Herr et al., 2019) and foraging on krill, any changes that affect the quantity and quality of their habitat and food availability could be significant. Currently, Antarctic minke whales and humpback whales are thought to partition prey resources in this region by feeding in different habitats (sea ice versus open water) but when the two species do overlap in time and space, they partition prey vertically (Friedlaender et al., 2008). With continued sea ice decline, the potential for overlap, and thus competition for prey, increases as does the likelihood that krill abundance will decrease due to poor recruitment, for example (Atkinson et al., 2004). This could lead to both a limited amount of preferred sea ice habitat and limited prey availability, increasing the potential for competition with other krill predators (including humpback whales (Megaptera novaeangliae), crabeater seals (Lobodon carcinophaga), Antarctic fur seals (Arctocephalus gazella), as well as a variety of penguin, seabird, and fish species). In combination, this could mean that Antarctic minke whales will be displaced to regions that are currently covered by more sea ice and those that remain may be at higher predation risk from killer whales in open water (Higdon and Ferguson, 2009) and be in competition with other predators for a limited prey resource.
Due to their small size and relatively fast movements, minke whales only became a target of industrial whaling operations after the demise of the larger whale species, in the early 1970s (Horwood, 1990). Commercial whaling is carried out by Norway and Iceland (under objection and reservation to the 1986 moratorium agreed by the IWC, respectively), and subsistence hunts carried out by Greenland. Until recently, when Japan decided to leave the IWC (Normile, 2019), whaling for minke whales also continued as part of Japan’s special permit (“scientific”) whaling programme. Overall, since 1985, 43,799 minke whales have reportedly been killed in commercial (25,583), special permit (15,176) and aboriginal (5,094) whaling programmes, respectively1. The scientific whaling by Japan occurred under Article VIII of the International Convention for the Regulation of Whaling (ICRW) and had long been criticized by other member states and scientific expert panels (Gales et al., 2005; Brierley and Clapham, 2016). The criticism, with which the authors of this review are in agreement, called into question the validity of the science being conducted, as well as made the accusation of the use of minke whaling and the sale of its products as a cover up for illegal trade with products from other protected species (Baker et al., 2000, 2010). In 2014 these long-standing concerns led Australia and New Zealand to bring the issue of whether Japan’s whaling is legitimately for scientific purposes before the International Court of Justice (ICJ), which declared in majority that Japan’s whaling programme at the time (JARPA II) was not “for the purposes of scientific research.” Despite this ruling and continued criticism of lack of scientific justification (Brierley and Clapham, 2016; Clapham, 2017), Japan’s current whaling programmes in the Antarctic (NEWREP-A) and North Pacific (NEWREP-NP) were implemented in seasons 2015/16 and 2017/18, respectively, with quotas to kill 333 Antarctic minke whales and 174 common minke whales in the North Pacific2. With its decision to leave the IWC, it is anticipated that Japan’s current “scientific” whaling programmes will stop and be replaced by a commercial whaling programme in their Exclusive Economic Zone (EEZ) (Normile, 2019).
With the advent of larger, faster moving ships since the 1950s, there has been a steady increase in ship strikes of baleen whales, which is likely to continue to increase as ships become even faster and quieter (Laist et al., 2001; McKenna et al., 2012; Monnahan et al., 2015). Minke whale mortality events attributed to ship strikes are usually characterized as blunt trauma (i.e., from ships colliding with the animal) or propeller cuts and lacerations. A study assessing large whale serious injury and mortality along the east coast of the United States from 1970 to 2009, documented that 17 out of 396 (4.3%) of documented minke whale mortality events were due to ship strikes (van der Hoop et al., 2012). Biases and under reporting of ship strike incidents suggest that many more fatal and non-fatal ship strikes occur than are documented (Peel et al., 2018). National and international ship strike databases are now being developed (Cates et al., 2017). More comprehensive, and in some regions, mandatory reporting practices are expected to improve our understanding of this serious problem for whale populations, including minke whales.
Over the last few decades, the potential impacts of human-made noise in the marine environment have raised concerns and received increased attention from scientists, conservationists, resource managers, policy makers and the public. Sources of anthropogenic noise are numerous and include military and scientific sonar, seismic surveys, underwater explosions, offshore construction and platforms, scientific research, pingers, and acoustic deterrent devices (ADDs), as well as shipping and vessel traffic (Prideaux, 2017). Measurements of ambient noise levels have shown that low-frequency noise has been steadily increasing, based on recordings analyzed from the 1960s to 2000s in the Northeast Pacific (Andrew et al., 2002; McDonald et al., 2006a), and from 2002 to 2012 in the Indian Ocean (Miksis-Olds et al., 2013). These increases in low frequency noise were primarily driven by shipping noise and noise from seismic air guns.
Information about minke whale hearing capabilities is very limited, as audiograms for large whales cannot be measured directly. Predictions of sensitivity to noise are therefore modeled or inferred from species-specific vocalizations, behavioral responses to sounds or anatomical measurements (Mellinger et al., 2000; Tubelli et al., 2012; Yamato et al., 2012; McGarry et al., 2017). Estimates of audiograms for baleen whales, including minke whales, assume highest sensitivities between 200 and 19,000 Hz (National Marine Fisheries Service, 2016). Simulations of the middle-ear transfer function (METF) of the minke whale auditory pathway suggested the best frequency range between approximately 30 and 25,000 Hz (Tubelli et al., 2012). A recent study in the Northwest Atlantic, investigated the potential of vessel noise to mask baleen whale vocalizations and found an ∼80% loss of communication space for minke whale pulse trains relative to historical “quiet” conditions (Cholewiak et al., 2018). Off Scotland, minke whale densities have been observed to decrease during naval exercises, and mortalities of minke whales occurred during at least two mass stranding events that have been linked to military sonar exercises (Parsons et al., 2000; Balcomb and Claridge, 2001). Minke whales have been observed to respond to mid-frequency active sonar by reducing or ceasing calling and by exhibiting avoidance behaviors (e.g., movement away from the sound source) even at relatively low received sound levels (Martin et al., 2015; Sivle et al., 2015; Kvadsheim et al., 2017). Also, results of a recent behavioral response study indicated that minke whales strongly avoided ADDs that are used in the context of noise mitigation of construction activities (McGarry et al., 2017).
Marine Litter and Chemical Pollution
Human caused pollution is a pervasive and increasing threat to marine environments (Laist, 1997; Hardesty et al., 2015). It has been estimated that more than six million metric tons of plastic enters the oceans each year; this is predicted to increase 10-fold within the next decade (Jambeck et al., 2015). Ingestion of plastic marine debris has been reported in nine species of baleen whales, including minke whales. Effects range from non-discernible pathological impacts to complete blockage of the digestive tract resulting in malnutrition, starvation and in some cases, mortality (Laist, 1997; Baulch and Perry, 2014). Although levels of persistent organic pollutants (POPs) are decreasing in some populations (Lebeuf et al., 2014), they are of concern to many cetacean species, who may accumulate high concentrations in their blubber (Jepson and Law, 2016). Baleen whales, including minke whales, typically feeding on lower trophic levels than toothed whales, have comparatively lower blubber POP concentrations (Elfes et al., 2010). Nonetheless POPs may have adverse effects on health and reproduction of populations of both species groups (Moon et al., 2010; Hall et al., 2018), especially in combination with other stressors (Côté et al., 2016).
Entanglement in Fishing Gear
Entanglement in fishing gear is another global problem, affecting a wide range of marine mammal species (Laist, 1997; Read, 2008; Baulch and Perry, 2014; Meager, 2016). Partly due to higher abundance compared to other species in some areas, minke whales are the species most frequently reported dead due to entanglement in fishing gear (Ryan et al., 2016). In Scotland, for example, evidence of entanglement in static fishing gear was present in as many as 50% of stranded minke whales examined from 1990 to 2010 (Northridge et al., 2010). Particularly high levels of by-catch and entanglement of the J stock population of minke whales, inhabiting the Sea of Japan, Yellow Sea, and East China Sea, have raised serious concerns in the IWC Scientific Committee in recent years (International Whaling Commission, 2010; Song et al., 2010). In South Korea, by-caught minke whales can legally be sold and a reporting system has been in place there since 1994. Although reporting of animals is not always accurate, these data show that from 1996 to 2014, minke whales by-caught in Korean waters alone exceeded the estimated level of potential biological removal (PBR) for this population (Song, 2016). Due to their small size, minke whales are more likely to die as a result of entanglement than other species, as they are less likely to be able to reach the surface when weighted down by fishing gear and more often sink after death, which may also lead to under-reporting of entanglement cases for this species (Knowlton et al., 2016). It has been estimated that 70% of entanglement cases for this species are fatal (Lien, 1994). More recently, several studies have highlighted the long-term consequences of entanglement and animal welfare implications for individuals, often suffering serious health effects over many years, and urged policy and management action to be more inclusive of these issues (Cassoff et al., 2011; Moore and van der Hoop, 2012; Dolman and Moore, 2017; Dolman and Brakes, 2018).
Whale watching tourism with a particular focus on minke whales occurs in several high latitude regions worldwide based on seasonal feeding aggregations (e.g., West Scotland, Iceland, Canada’s Gulf of St. Lawrence), as well as in Australia’s Great Barrier Reef, which provides habitat for a presumed breeding aggregation of dwarf minke whales (Valentine et al., 2004; O’Connor et al., 2009). Whale watching of minke whales is typically vessel-based, with the Great Barrier Reef case being a unique swim-with activity, that has been managed by the Great Barrier Reef Marine Park Authority since 2003 (Valentine et al., 2004; Mangott et al., 2011; Curnock et al., 2013). To better understand the potential impacts of vessel-based tourism interactions on minke whales and other baleen whales, recent research has focussed largely on behavioral responses to vessels, including changes in swim speed and direction, diving behavior, and decreased time spent resting or feeding (New et al., 2015). Relatively few studies have investigated direct physiological effects associated with disturbance from vessels, including from direct vessel approaches (Christiansen et al., 2014), vessel noise (Erbe, 2002), and vessel pollutants such as oil leaks and exhaust emissions (Lachmuth et al., 2011). While some effects have been inferred, for example increased stress levels and energy expenditure among minke whales in the presence of whale watching vessels (Christiansen et al., 2014), longer-term chronic and cumulative effects of whale watching are of potentially greater concern, but are difficult to assess and thus remain largely unstudied and unknown (Bejder et al., 2006; New et al., 2015).
Monitoring and Research Approaches
Visual Monitoring and Behavioral Studies
Visual monitoring, from boats, ships or airplanes, is still one of the most common approaches to study marine mammal distribution and abundance (Barlow, 2015; Hammond et al., 2017). Despite recent advances in visual monitoring methods (Ferguson et al., 2018), these approaches always will be limited for monitoring animals that spend a large proportion of their lives under water (Borchers et al., 2013; Thomson et al., 2013). In addition, visual surveys are dependent on daylight, and good sighting and weather conditions, and are often spatially restricted to coastal areas. Therefore, they can only provide a snapshot of the true distribution, particularly for far-ranging species such as minke whales (Kaschner et al., 2012). In part due to such limitations and their small size and inconspicuous blows and behavior, knowledge on long-term minke whale distribution and abundance, especially during winter, is still sparse (Best et al., 2012).
Research on dwarf minke whales has largely been based on a small population wintering in the Great Barrier Reef, utilizing dive tourism vessels as platforms of opportunity. Despite the limitations associated with the use of such platforms (i.e., non-systematic survey effort), the ability to study the whales from in-water, and the collection of long-term datasets (e.g., 1996 to present) has enabled a diverse and innovative research programme. Such research has included “interacting population” size estimation using mark-recapture modeling from photo-identified whales (Sobtzick, 2010), population demography via underwater videogrammetry (Sobtzick, 2010) behavioral studies (Mangott et al., 2011), passive acoustic monitoring (PAM) (Gedamke et al., 2001), social and economic valuation of the swim-with-whales tourism activity (Stoeckl et al., 2010), applied research for adaptive management (Curnock et al., 2013), and recently, genetics, migration and habitat use studies via biopsies and satellite-tagging (Birtles et al., 2015).
Photo-identification has been used to recognize and re-sight individual common minke whales since the late 1970s (Dorsey, 1983). Individual identification from surface photography typically relies on clear images of dorsal fin profiles, body scars and pigmentation patterns, and the technique has been used to establish seasonal and inter-annual site fidelity and residency times in a number of feeding areas, for example the east and west coasts of North America (Dorsey, 1983; Stern et al., 1990), and the Isle of Mull, Scotland (Gill et al., 2000). Underwater photo-identification of dwarf minke whales in Australia’s Great Barrier Reef, ongoing since 1996 (Arnold and Birtles, 1999), is based primarily on lateral pigmentation patterns which have been shown to have sufficient individual variability and long-term stability, akin to humpback whale flukes (Arnold et al., 2005; Sobtzick, 2010). Due to their interactions with tourists and the growing popularity of underwater photography, there is a significant “citizen science” component to this photo-identification programme, to which tens of thousands of images are now contributed each winter season (Sobtzick, 2010; Birtles et al., 2014). Mark-recapture modeling has provided an estimate of the “interacting population” (noting an unknown proportion of whales that do not interact voluntarily with vessels and swimmers) over three seasons, consisting of several hundred animals each year (Sobtzick, 2010). Due to an increasing quantity of images collected annually, the manual image matching process is not cost-effective for some larger populations, and new pattern recognition algorithms may provide a solution to this problem. Konovalov et al. (2018) report on a “proof of concept” for recognizing individual dwarf minke whales using the Deep Learning Convolutional Neural Networks tool. Further advancements in the use of such technology may lead to a viable alternative to manual photo analysis in the near future.
Satellite Tags, Multisensor Tags, and Unmanned Aerial Systems (UAS)
Technological advances are improving our ability to measure and understand the biology of minke whales around the world. Although not necessarily novel, satellite telemetry is a key tool for collecting data that improves our understanding of the broad-scale movement patterns, behaviors, and associations between individuals and their environment over times that are relevant to the biology of the species. Information from satellite tags can provide insights on critical and preferred habitats. From foraging to migration, satellite tags offer a unique perspective on minke whales over extended spatio-temporal ranges that cannot be easily obtained using other methods (Birtles et al., 2015; Víkingsson and Heide-Jørgensen, 2015).
The advent of smaller multi-sensor recording tags has revolutionized our ability to quantify and provide detailed information on the underwater behavior of diving animals. For example, researchers are now able to observe and measure the feeding rates of minke whales (e.g., Friedlaender et al., 2014). These motion-sensing tags (which can also include point-of-view video) allow for unprecedented measurement of the kinematics, speed, maneuverability, energy expenditure, and even information on the habitat of diving animals (Friedlaender et al., 2009, 2014, 2016; Goldbogen et al., 2015, 2017; Cade et al., 2016). The ability to measure the fine-scale movement and behavior of minke whales is critical to providing quantitative information on their energetic needs, daily behavior, and potential for being impacted by environmental change.
Unmanned aerial systems (UAS) are an emerging technology that can be used in a number of different capacities to collect valuable information on minke whales and their habitats. UAS have been shown to be able to accurately measure not only the total length of individual marine mammals, but also their general health condition (Christiansen et al., 2016; Durban et al., 2016). This information is critical to being able to extrapolate to the population-level regarding the age-class distribution, individual health measures, and overall fitness of a population. UAS are also being used to collect expired breaths from marine mammals that can be chemically evaluated to measure hormone levels and even extract DNA (Pirotta et al., 2017). This information is useful for determining stress and pregnancy as well as the population of which an individual is a part. UAS can also be used to survey smaller areas at high-resolution with accurate geo-referencing. This information is critical when linking the small-scale movement patterns and behavior of animals to their environment as such surveys can provide insights as to the amount of available habitat in an area.
Passive Acoustic Monitoring (PAM)
Minke whales are known to produce a variety of sounds across their geographic range. In the North Atlantic, frequency-modulated downsweeps and low-frequency pulse trains with varying inter-pulse interval structure have been attributed to minke whales (Beamish and Mitchell, 1973; Edds-Walton, 2000; Mellinger et al., 2000). In the early 2000s, the North Pacific “boing” sound was identified as a minke whale call (Rankin and Barlow, 2005), and more recently low-frequency downsweep and pulse-train sounds were described from recordings made in British Columbia, Canada (Nikolich and Towers, 2018). Australian dwarf minke whales produce a complex call, dubbed the “star wars” vocalization (Gedamke et al., 2001; Figures 2A–C). In the southern hemisphere, the “bioduck signal” (Figures 2D,E), which had been recorded in the Southern Ocean for decades, has recently been attributed to the Antarctic minke whale (Risch et al., 2014b).
Figure 2. Spectrograms of known minke whale vocalizations from different oceanbasins. (A) North Atlantic slow-down pulse trains, (B) North Pacific “boing” vocalization, (C) Australian dwarf minke whale “star wars” vocalization, (D) Antactic “bioduck,” (E) Antarctic downsweeps. Note different time and frequency scales. Spectrogramparameters: (A) Fast Fourier Transform (FFT) = 1024 pt, overlap (ovlp) = 75%,samplerate (SR) = 2000 Hz: frequency resolution (FR) = 1.9 Hz, time resolution (TR) = 128 ms; (B) FFT = 512 pt, ovlp = 75%, SR = 8000 Hz: FR = 15.6 Hz, TR = 16 ms; (C) FFT = 512 pt, ovlp = 75%, SR = 16,000 Hz: FR = 31.5 Hz, TR = 8 ms; (D) FFT = 1024pt, ovlp = 75%, SR = 4000 Hz: FR = 3.9 Hz, TR = 64 ms; (E) FFT = 4096 pt, ovlp = 75%, SR = 25,811 Hz: FR = 6.3 Hz, TR = 39 ms.
As mentioned above, visual surveys for marine mammals are carried out mostly during daylight and summer months, leaving large data gaps for many species’ winter distribution and daily habitat use. Long-term PAM surveys have been shown to be capable in filling some of these gaps and are particularly useful for the study of cryptic species that are difficult to detect visually, such as minke whales (e.g., Risch et al., 2019). Recent advances in digital signal acquisition and processing, increased storage capacity, and reduced power consumption and instrument size means that PAM is increasingly complementing visual surveys of marine mammals (Clark et al., 2010; Gerrodette et al., 2011). Towed hydrophone arrays are now commonly used on marine mammal surveys, and in some cases, the passive acoustic data collected have been used for estimates of relative abundance of minke whales (Barlow and Taylor, 2005; Norris et al., 2017). Large-scale networks of bottom-mounted hydrophones and autonomous acoustic recorders have been used to investigate migratory routes, changes in distribution and to describe previously unknown habitats of baleen whales (Clark and Gagnon, 2004; Risch et al., 2014a; Davis et al., 2017). Time-synchronized hydrophone arrays are now being used in semi-automated approaches to localize and even track individual animals (Martin et al., 2017). Where detailed knowledge on the vocal behavior (e.g., calling or cue rate) of the target population exists, PAM can be used to estimate densities of animals (Lewis et al., 2007; Efford et al., 2009; Marques et al., 2013; Harris et al., 2018). For example, passive acoustic data has been used to estimate relative abundance of North Pacific minke whales in a small area using their “boing” vocalizations and applying cue-counting methods using the calling rate from a single tracked individual (Martin et al., 2013).
The recent development of these new statistical methods for density estimation based on PAM data show great promise for monitoring minke whales in challenging offshore, remote, and sometimes ice-covered habitats. However, several assumptions must be met and parameters, such as cue rates, need to be known in order to reliably estimate animal abundance from passive acoustic data (Marques et al., 2013). However, the vocalization rate for most marine mammals, including minke whales can be quite variable (Oleson et al., 2007; Parks et al., 2011b), making it difficult to estimate accurate and robust cue rates. Techniques to overcome these challenges include collecting data using acoustic tags and behavioral focal follow studies (Johnson et al., 2009; Parks et al., 2011a).
In addition to monitoring population abundance, PAM data can be used for exploring geographic variability in vocalizations with the potential to reveal population structure (Rankin and Barlow, 2005; McDonald et al., 2006b), migration routes (Norris et al., 1995; Risch et al., 2014a), habitat use and environmental correlates (Baumgartner and Fratantoni, 2008; Stafford et al., 2009) as well as for the study of behavior and the impact of anthropogenic activities (Forney et al., 2017).
Conservation Status and Management Approaches
Although abundance estimates are missing for large parts of their known distributional range, common minke whales are currently listed as a species of Least Concern (LC) under the International Union for Conservation of Nature (IUCN) Red List (Cooke et al., 2018a). The Convention on International Trade in Endangered Species (CITES) lists all common minke whale populations under Appendix I (threatened with extinction), with the exception of the West Greenland stock, which is listed under Appendix II (not currently threatened but trade needs to be strictly regulated).
Latest best estimates by the International Whaling Commission (IWC) are 90,000 (CI = 60,000–130,000) for the eastern North Atlantic; 50,000 (CI = 30,000–85,000) for the central Atlantic, and 17,000 (7,000–40,000) for West Greenland3. The most recent abundance estimate for the Canadian East coast stock is 2,591 (CV = 0.81) animals (Hayes et al., 2018). It has been suggested, that there may be two separate breeding populations in the North Atlantic (Anderwald et al., 2011), but no definite breeding grounds have yet been confirmed. Other studies have found no evidence for population structuring in the North East Atlantic but highlighted the importance of analysis of more genetic markers to answer the question conclusively (Quintela et al., 2014).
The North Pacific has generally been surveyed less and population estimates are thus patchy. The most recent analysis of inshore ship line transect surveys from the US west coast (Washington to California) estimated 636 (CV = 0.72) animals (Carretta et al., 2017). A passive acoustic line-transect survey of the Northern Mariana Islands estimated between 80 and 91 animals (CV = 0.34) for this area in winter and spring (Norris et al., 2017). Because acoustic estimates are based on vocalizations believed to be produced only by males, these are considered minimum estimates. The latest IWC “best” estimate for the western North Pacific and Okhotsk Sea is 22,000 (CI under review) animals3. At least two sub-populations are currently recognized in the western North Pacific, although acoustic records suggest that further population structure might exist (Rankin and Barlow, 2005). While the sub-population called “J stock” inhabits the Yellow Sea, East China Sea and the Sea of Japan, “O stock” inhabits more offshore waters of the Northwest Pacific and the Okhotsk Sea (Kato, 1992). There has been serious concern and debate within the IWC about the status of J stock, which in addition to being targeted by whaling operations, is also frequently caught incidentally in fishing gear (Song, 2016; Cooke et al., 2018a). The current minimum population estimate for this population is 5,247 animals (Song, 2016).
The abundance of dwarf minke whales in the Southern Ocean has not been assessed systematically, because in the past most sighting surveys and whaling records did not distinguish it from the Antarctic minke whale (Cooke et al., 2018a). For example, the IWC sightings surveys carried out in the Southern Ocean (IDCR-SOWER) identified only a small percentage of minke whale sightings as dwarf minke whale (Branch and Butterworth, 2001). To our knowledge, the only abundance estimate of a dwarf minke whale population to date is from the Great Barrier Reef, where photo-ID data collected over 3 years suggested a yearly fluctuating “interacting population” size of between 342 and 789 individuals (Sobtzick, 2010).
The most recent estimate of overall abundance of Antarctic minke whales is around 500,000 individuals, down from an estimated 720,000 in earlier assessments (International Whaling Commission, 2013). Notwithstanding a lack of confidence in parts of this assessment, this represents a 31% decline, the direction and reasons of which currently are unknown. There is also disagreement as to whether current abundance estimates are similar to pre-whaling abundance figures. One of the difficulties in generating abundance estimates for this species is due to its affinity for sea ice, as has been shown by recent aerial surveys (Williams et al., 2014; Herr et al., 2019). Despite these logistical challenges and ongoing discussions, current population estimates and their trajectory give reason for concern and accordingly have resulted in the recent classification of Antarctic minke whales as Near Threatened under the IUCN Red List and under Appendix I of CITES (Cooke et al., 2018b).
Combining the effects of various anthropogenic pressures on individuals and populations and addressing them in a cumulative context still presents a considerable challenge, in urgent need of new scientific and conservation approaches (Côté et al., 2016). This is especially true for highly mobile species and when disturbances change over space and time. Several frameworks such as the Population Consequences of Disturbance (PCoD) model (Pirotta et al., 2018) have been developed in recent years. These models attempt to link health effects of combined pressures with vital rates that can be scaled up to population consequences but are still often limited by our ability to accurately parameterize parts of the model and deal with uncertainties. While new research and innovations in methods, tools and techniques are needed to address the many outstanding information deficiencies, long-term monitoring of populations and the pressures to which they are exposed, provides vital feedback on the effectiveness of management policies and actions. Such monitoring must be integrative, encompassing not only abundance estimates of the whales, but also components of the wider system in which they live, including natural and anthropogenic pressures. In practice, these types of monitoring programmes and adaptive management approaches are scarce. However, an example of such a programme has recently been applied in the Great Barrier Reef, which uses the Driver, Pressure, State, Impact, and Response (DPSIR) framework to identify and connect appropriate indicators for monitoring and enhancing the system-wide understanding (Great Barrier Reef Marine Park Authority, 2015). Developed in the late 1990s by the European Environmental Agency (EEA), DPSIR provides an integrative model for monitoring and assessment of linked social-ecological systems at multiple scales (Gari et al., 2015). Within DPSIR, Drivers are the overarching causes and trends that influence a range of events/activities that exert Pressures on parts of the system (e.g., climate change influences storm intensity, and coastal development influences ocean pollution). State represents the condition of a value (e.g., a characteristic of a whale population, such as abundance, health, reproduction, etc.) that can/will respond to pressures and change over time, whereas Impact is considered to be the resultant effect to human well-being that flows from a change in the state of a value (e.g., a loss of cultural, economic or heritage value associated with a whale population). Responses are actions taken by resource managers and/or communities to influence drivers, mitigate pressures and/or restore the state of values (Carr et al., 2007; Tscherning et al., 2012; Gari et al., 2015). The development of an integrated monitoring programme for the Great Barrier Reef utilizes DPSIR to identify relationships and processes between system components (e.g., whales and shipping, agriculture and corals, etc.) assisting with identification of knowledge gaps, barriers to effective management and the prioritization of monitoring effort (see Figure 3).
Figure 3. Example Driver, Pressure, State, Impact, and Response (DPSIR) flowchart identifying system components and relationships relevant to integrated monitoring of dwarf minke whales in the Great Barrier Reef World Heritage Area (adapted from Curnock et al., 2018, for illustrative purposes).
Conclusion: Data Gaps, Research, and Monitoring Priorities
The expansive, seasonally changing distribution patterns of many minke whale populations, means that they are exposed to a number of anthropogenic threats throughout their range. Pressures vary in type and severity in different habitats and are often cumulative, making it difficult to protect such highly mobile populations, especially when large parts of their year-round distribution are unknown.
A priority for future research should therefore be to better understand migratory routes and seasonal habitats, in particular winter breeding grounds, of minke whale populations worldwide. Such efforts should focus on populations that are currently commercially exploited or threatened, like those in the Northwest Pacific, and those that are currently not being monitored, such as almost all populations of dwarf minke whales. In the case of Antarctic minke whales it is important to better understand their in-ice distribution and its effects on current population estimates. Dedicated and opportunistic PAM networks are recommended to define migration corridors, identify currently unknown offshore habitats and monitor longer-term changes in distribution (see Davis et al., 2017). In this context, a better understanding of the full vocal repertoire, especially behavioral and density dependent variability in calling rates will also be important.
Both common minke whales in the Arctic and Antarctic minke whales show sexual segregated migration with females generally moving toward higher latitudes (Horwood, 1990; Laidre et al., 2009). A better understanding of such behavior is important for species monitoring and assessing impacts of ongoing whaling operations. Non-lethal new technologies such as PAM, UAS, multi-sensor and satellite tags can help to address such knowledge gaps even in challenging remote and offshore habitats.
Entanglements in fishing gear and ship strike are affecting baleen whale populations worldwide, but the extent of these impacts and how they relate to other pressures are rarely fully understood. The case of the J-stock population of common minke whales in the Northwest Pacific is an example of interactions of pressures putting a small population at risk for survival. Japan’s announced withdrawal from the IWC in December 2018 potentially places even more pressure on this endangered (and other) populations in their EEZ.
Finally, climate change and its effects on global oceanic ecosystems are changing environmental and anthropogenic pressures that determine migratory routes and species habitats at an increasingly faster pace (Tulloch Ayesha et al., 2019), requiring flexible and adaptable conservation approaches. Across species, comparative and multi-disciplinary approaches are thus necessary to conserve minke whale populations worldwide.
DR coordinated this work. All authors (DR, MC, TN, and AF) contributed to writing and editing the work.
Conflict of Interest Statement
TN was employed by Bio-Waves Inc.
The remaining 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.
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Keywords: population status, minke whales, Antarctic minke whale, conservation, future research
Citation: Risch D, Norris T, Curnock M and Friedlaender A (2019) Common and Antarctic Minke Whales: Conservation Status and Future Research Directions. Front. Mar. Sci. 6:247. doi: 10.3389/fmars.2019.00247
Received: 07 December 2018; Accepted: 24 April 2019;
Published: 14 May 2019.
Edited by:Rob Harcourt, Macquarie University, Australia
Reviewed by:Luis Cardona, University of Barcelona, Spain
Salvatore Cerchio, New England Aquarium, United States
Copyright © 2019 Risch, Norris, Curnock and Friedlaender. 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.
*Correspondence: Denise Risch, email@example.com