Between the 8th January and the 25th February 2016, the largest sperm whale Physeter macrocephalus mortality event ever recorded in the North Sea occurred with 30 sperm whales stranding in five countries within six weeks. All sperm whales were immature males. Groups were stratified by size, with the smaller animals stranding in the Netherlands, and the largest in England. The majority (n = 27) of the stranded animals were necropsied and/or sampled, allowing for an international and comprehensive investigation into this mortality event. The animals were in fair to good nutritional condition and, aside from the pathologies caused by stranding, did not exhibit significant evidence of disease or trauma. Infectious agents were found, including various parasite species, several bacterial and fungal pathogens and a novel alphaherpesvirus. In nine of the sperm whales a variety of marine litter was found. However, none of these findings were considered to have been the primary cause of the stranding event. Potential anthropogenic and environmental factors that may have caused the sperm whales to enter the North Sea were assessed. Once sperm whales enter the North Sea and head south, the water becomes progressively shallower (<40 m), making this region a global hotspot for sperm whale strandings. We conclude that the reasons for sperm whales to enter the southern North Sea are the result of complex interactions of extrinsic environmental factors. As such, these large mortality events seldom have a single ultimate cause and it is only through multidisciplinary, collaborative approaches that potentially multifactorial large-scale stranding events can be effectively investigated.
Citation: IJsseldijk LL, van Neer A, Deaville R, Begeman L, van de Bildt M, van den Brand JMA, et al. (2018) Beached bachelors: An extensive study on the largest recorded sperm whale Physeter macrocephalus mortality event in the North Sea. PLoS ONE 13(8): e0201221. https://doi.org/10.1371/journal.pone.0201221
Editor: David Hyrenbach, Hawaii Pacific University, UNITED STATES
Received: March 8, 2018; Accepted: July 11, 2018; Published: August 7, 2018
Copyright: © 2018 IJsseldijk et al. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Data Availability: All relevant data are within the paper and its Supporting Information files.
Funding: Necropsies and stomach content analysis in the Netherlands were conducted through funding gained from the Dutch Ministry of Economic Affairs (grant number: HD3611/BO11018.02 065). UK necropsies and sampling were conducted by the UK Cetacean Strandings Investigation Programme, which is co-funded by Defra (Marine Biodiversity division) and the Devolved Governments of Scotland and Wales (contract number MB0111). The necropsy in France was funded by Agence Française pour la Biodiversité and Ministère de la Transition Ecologique et Solidaire. In addition, the Ministry of Energy, Agriculture, the Environment and Rural Areas of Schleswig-Holstein, the State Agency of Coastal Protection, National Parks and Ocean Protection of Schleswig-Holstein as well as the Federal Ministry of the Environment, Nature Conservation, Building and Nuclear Safety funded the work on the animals in Schleswig-Holstein. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Cetacean strandings occur across all the world’s oceans and have been recorded throughout history . Some stranding events attract curious crowds, and questions are often raised about potential causes. Stranding events can consist of an individual live or dead cetacean and less frequently of multiple live and/or dead animals . One of the species known to be involved in such mass stranding events is the sperm whale Physeter macrocephalus.
The sperm whale is a widely distributed species, inhabiting deeper waters from the equator to the polar regions. Commercial whaling from the 1800’s to the 1960’s significantly reduced populations, with a global pre-whaling population estimate of 1,100,000 reduced by approximately 67% . Since the moratorium on commercial whaling in the 1980’s, the current global population size is estimated at around 360,000 individuals (coefficient of variation = 0.36) with no evidence of a notable increase or reduction [3,4]. Sperm whales show distinct spatial population segregation, with females and calves normally resident year-round near breeding areas around the equator, and males migrating between the breeding areas and high-latitude feeding grounds [4,5,6,7].
Male sperm whales usually migrate along the Faeroe—Shetland Channel on their southward migration [8,9]. Some animals may enter the Norwegian trench during their southern migration and mistakenly enter the North Sea region. This is a potentially hazardous region for a pelagic species: the North Sea becomes much shallower and narrower towards its southern margin, with gradually sloping coastlines, sandbanks and tidal mudflats with high tidal amplitudes  (S1 Fig). Numerous historical sperm whale strandings around the North Sea have been documented, with this region being recognized as one of the global hotspots for sperm whale strandings. Smeenk  documented all recorded sperm whale strandings in the North Sea from 1560 until 1995. Most stranding events involved one to three sperm whales in the same location, while large mortalities in this area have been relatively uncommon [5,11].
A systematic pathological examination of single and mass stranded marine mammals may help to elucidate the cause of strandings and to investigate the general health status of marine mammal species (e.g. ). Standardised necropsies of cetaceans have demonstrated a wide range of infectious diseases, physical trauma, and metabolic or dietary derangements [13–15]. In addition, several direct and indirect effects of anthropogenic activities on the health of cetaceans have previously been described [16–20]. However, knowledge on the health status of sperm whales is still scarce and little pathological data has been published. Previous strandings of sperm whales have been linked to navigational errors ; solar storms [22,23]; climate events ; gastric impaction from plastic ingestion ; potential seismic surveys , contaminants  and disease [9,28, 29].
In early 2016, the largest sperm whale mortality event ever recorded in the North Sea region occurred, with 30 whales stranded in five countries over a period of six weeks. This stranding event allowed the systematic collection of information on the biology and health status of a large number of animals. Through a comprehensive pathological investigation, comprising gross post mortem assessment and a range of ancillary diagnostic tests, we investigated the hypothesis that this stranding event could be explained by a compromise in the health status of one or more of the stranded animals. Elimination of disease as a plausible cause of these strandings would suggest that other natural or anthropogenic factors were influential in this mortality event and we discuss potential contributing factors. In addition, and with the aim of placing this mortality event into historical context, we provide an update of the historical time series (published by Smeenk ) with sperm whale stranding reports from the last twenty-one years (1996–2016) in the southern North Sea region.
Materials and methods
The animals described in this study were not used for scientific or commercial testing. All were free-living whales which died of natural causes. No consent from an Animal Use Committee is therefore required. Consequently, animal ethics committee approval was not applicable to this work.
Comprehensive gross necropsies were carried out on 23 sperm whales and additional sampling was conducted in four others. Three sperm whales could not be studied due to logistical constraints. Necropsies and histopathological studies were conducted following standard procedures [13,14,30,31].
The nutritional status was visually assessed based on the dorsal musculature and through quantitative assessment of blubber thickness, measured, where possible, immediately anterior to the dorsal fin at three locations (dorsal, lateral and ventral). Necropsies and sampling of the carcasses were performed with intervals between stranding and investigation ranging from 11 hours to eight days. Due to the significant logistical challenges in undertaking multiple beach necropsies and the rapid decomposition rate for this large species, in combination with likely peri mortem hyperthermia from live stranding, decomposition of the carcasses constrained the evaluation of the major organs and extensive histopathological assessment in most cases. The decomposition condition codes (DCC) of the carcasses at the point of necropsy were assessed following internationally standardised guidelines (, with DCC1 representing very fresh carcasses and DCC5 the skeletal remains of animals). The freshest animals were necropsied in the Netherlands (DCC1-3), while in Germany most carcasses were DCC4 at the time of examination. The majority of the necropsied whales in England and the one in France were DCC3-4.
Samples for histopathology were collected from all animals which were in a fresh to moderate state of decomposition (DCC1-3). Tissues available for histologic review varied from animal to animal, but included: eye (with optic nerve), skin (with any lesions), muscle, pre scapular lymph nodes, lung and associated lymph nodes, heart, liver, adrenals, kidney, oesophagus, stomachs, spleen, pancreas, intestine and associated lymph nodes, reproductive tissue and associated lymph nodes, and, if possible, brain and spinal cord. Tissues were routinely embedded in paraffin, sectioned at 4–7 mm, stained with hematoxylin and eosin (HE), and examined microscopically at the facility of origin. Additional staining was performed when appropriate, including the Periodic acid–Schiff stain to detect polysaccharides, the Von Kossa stain to quantify mineralization, and the Iron stain.
In 74% (20 / 27) of the cases, a mandibular tooth was collected during field sampling and subsequently analysed to determine age according to methods described . In short: teeth were sectioned along the bucco-lingual plane and one half-section polished and etched in 15% formic acid until the growth layer groups could be read.
Parasite presence and magnitude of infection was assessed macroscopically and rated as none (no parasites observed), mild infections, moderate infections or severe infections (following [13,33]). Parasites were collected and stored in 70% alcohol before morphological identification to genera level [34,35] using a stereomicroscope (Olympus SZ61), with additional species identification confirmed by molecular techniques in some cases. Parasitic infections were confirmed by histology and the severity of associated lesions caused by the parasites were recorded. Molecular identification was conducted after DNA isolation, PCR amplification and sequencing. Results were analysed with BioEdit (version 7.2.5) , MEGA 4  and BLAST on GenBank .
Samples from lung, liver, kidney, spleen, intestine, intestinal lymph nodes and any additional lesions identified at gross examination were subjected to microbiological examination, conducted according to standard protocols  from 15 sperm whales. Selective media was used to identify Brucella spp. .
Virological examinations were conducted on 10% organ homogenates, made by homogenisation in transport medium (Kinematica Polytron). Total nucleic acids were isolated from 200 μl of homogenates or swab transport medium using the MagnaPure LC Total Nucleic Acid Isolation Kit (Roche Diagnostics). TaqMan RT-PCR was performed using primers and probe specific for the Influenza Matrix gene . For morbillivirus reverse transcriptase PCR primers were used recognizing a phosphoprotein gene fragment . For herpesvirus PCR degenerate primers, recognizing a polymerase gene fragment, were used . Virus isolation was performed on the following cell lines and primary cell cultures: Vero DogSLAM , MDBK, TTKi, PPki, SeKC, CrFK. 100μl of 10% organ homogenates were inoculated on the different cell cultures and checked for cytopathic effects regularly, with 3 passages (7–10 days per passage) and cells and supernatants of the last passage were checked for morbillivirus and herpesvirus by PCR. Additionally, blowhole swabs from three whales were tested for herpesvirus as described above. The alignment of the partial polymerase gene (175 bp) of selected gamma- and alphaherpesviruses related mainly to cetaceans was performed with MAFFT alignment version 7 .
Assessment of tympanoperiotic complexes
Twelve cases were investigated for evidence of trauma to the auditory system by investigation of the tympanic-periotic bone complexes for fractures using high-resolution computerized tomography imaging according to . None of the inner ears could be investigated histologically for the presence of acoustic trauma due to logistical constraints and the fast decomposition of this tissue .
Diet studies and marine litter
Stomach contents were collected and analysed according to . Marine litter was investigated according to . In short: gastro-intestinal tracts were opened from stomach to anus and content was collected. The gastro-intestinal tracts of seven sperm whales were also rinsed and contents sieved over 500 and 1000 μm mesh. Contents of five of these animals were in addition machine-washed (following ) to dissolve organic materials and isolate hard prey remains (bones, otoliths and beaks) and foreign objects (such as plastic particles). All prey items were cleaned, identified to species where possible and measured. Based on squid beak and otolith measurements, prey remains were converted into biomass, according to [51,52].
A search for earthquakes with a magnitude of 4 or higher in the North Atlantic Ocean and North Sea was conducted using the online database from the European-Mediterranean Seismological Centre in the month prior to the first reported sperm whale stranding (01-12-2015–07-01-2016) (https://www.emsc-csem.org/Earthquake/?filter=yes) .
Data on sea surface temperature (SST) with a spatial resolution of 0.25 and respective anomalies were downloaded on 12-01-2018 from ftp://eclipse.ncdc.noaa.gov/pub/OI-daily-v2/NetCDF/ for the area ranging from N57.0-E10.0 to N68.0-E7.0. For details on the methods generating the SST data see . As it is not clear when the whales entered the North Sea, daily SST values were averaged over the entire area using R Version 3.4.0 x64  with the packages raster , sp  and ncdf4  and are shown with a 95% confidence interval.
Genetics and contamination profiles
Maternal relatedness and the putative origin was investigated by studying genetic diversity of 27 of the stranded sperm whales (details in ). Among 24 of these individuals, contamination profiles as an indication of social structures were also investigated (details in ).
To contextualise this mortality event, we added two decades of stranding records to the data published in 1997 . Stranding records were gained through national databases of Denmark (database of the University of Aarhus), the Netherlands (online database of Naturalis, Leiden; www.walvisstrandingen.nl), the United Kingdom (database of Cetacean Stranding Investigation Programme, London), Germany (database of Institute for Terrestrial and Aquatic Wildlife Research, Büsum), Belgium (database at the Belgian Marine Data Centre, Brussels) and through existing literature.
The first stranded animals were found on January 8th 2016 and 28 additional animals were subsequently reported up to February 21st 2016: sixteen in Germany; six in England; six in the Netherlands; one in France; and one in Denmark (Fig 1; Table 1). Twenty-seven percent (8 /30) of the animals were initially found alive, but died soon after stranding.
The asterisks indicate stranding locations, with the number of the stranded sperm whales referring to the strandings data presented in S1 Table. The colour palette represents the total depth of the area, with all dark red areas being <5 m (Bathymetry layer: ).
The table included case numbers, country (DE = Germany, DK = Denmark, FR = France, NL = the Netherlands, UK = United Kingdom, here England), stranding dates (all during 2016), stranding locations, decomposition condition codes (DCC) of the cases at the time of investigation, the date of the post mortem investigation, total length (TL, in m), age (in years), any significant pre-existing disease, evidence of trauma, results of gross ear examination, visual assessment of evidence of gas emboli, detection of Brucella spp. and Morbillivirus infections. NE = Not Examined. NAD = No Abnormalities Detected. U = Unable to examine due to decomposition condition.
All whales were immature males (spermatogenesis not present or not extensive), with a straight-line body length ranging from 9.6 to 14.7 m and an average of 11.7 m. Age was determined in 20 cases, and ranged between 10 and 16 years (Table 1).
Disease and pathogen investigation
Morphology and histopathology.
From macroscopic evaluation, all necropsied animals were judged to be in a fair to good nutritional condition. In 9/22 cases marine debris was found in the gastro-intestinal tract . No evidence of fractured or recently healed tympanic-periotic bone complex was detected in the thirteen animals investigated (ID # 1, 4, 5, 11, 18, 20–25, 27, 28 ). The state of preservation of most cases did not allow gas- and fat embolism analysis, but no visual evidence was found in the freshest cases (ID # 6–9, 29).
Histopathological findings included focal, severe dermatitis with epithelial degeneration in five sperm whales (ID # 6–10); congested dermal papillae in six sperm whales (ID # 11, 19, 21, 24, 25 and 28); and cutaneous haemorrhage with oedema in one (ID # 26). Five animals showed rake mark lesions on their tail flukes (ID # 4, 7, 18, 21, 23), one fresh enough to still be haemorrhagic upon discovery (ID # 23) while two others (ID # 18 and 21) presented bilateral and alternating lacerations, with inter-distance that resemble killer whale (Orcinus orca) interdental distances . This suggests possible recent interactions between these species. One sperm whale had hyaline myofiber degeneration (Zenker’s degeneration, rhabdomyolysis) (ID # 4) and extensive muscle damage and degeneration was apparent in an additional four whales (ID # 6, 7, 9 and 26). Histologic assessment of the kidneys revealed intratubular protein leakage and intravascular microthrombi in one sperm whale (ID # 6). Two animals demonstrated congestion and intensive centrilobular necrosis of the liver (ID # 6 and 9). Severe pulmonary oedema; intra-alveolar haemorrhages or lung congestion was confirmed in four cases (ID # 6, 9, 24 and 26). Two whales showed lymphoplasmacytic inflammation with partly eosinophilic inflammation (ID # 4 and 21), one animal had an acutely haemorrhagic tongue (ID # 10) and finally another whale showed focal vacuolar degeneration of the palatum durum epithelium (ID # 9). All changes were either associated with the stranding process or unlikely to have been severe enough to cause stranding (S1 Table).
All necropsied sperm whales had infections with single or multiple parasite species, but all infections were considered of low intensity (S2 Table). Most frequently found were infections with larval stages of Phyllobothrium delphini in the blubber of 21 sperm whales (ID # 1, 2, 4, 5, 7, 8, 11, 13–16, 18, 20–25, 27–29); infections with anisakid nematodes belonging to the genus Anisakis simplex sensu stricto in six sperm whales (ID # 6, 8, 9, 11, 16 and 29); infections with acanthocephalans, morphologically and molecularly identified as Bolbosoma capitatum, in nine sperm whales (ID # 4–10, 18 and 25); infections with Corynosoma curilensis of two sperm whales (ID # 5 and 25); infections with Chondracanthus lophii of two sperm whales (ID # 6 and 7) and the detection of one Pennella balaenopterae associated with a severe, pyogranulomatous, deep dermatitis around the anchoring location in one case (ID # 28). No significant gross or histological changes of the organs with parasitic infections were detected.
Virological examination resulted in the discovery of a novel cetacean alphaherpesvirus from blowhole swabs of three sperm whales (ID # 18, 20 and 24). No macroscopic or histologic lesions were identified. Four other cases (ID # 6–9) investigated for the presence of Influenza A virus, morbillivirus and herpesvirus did not result in further viral detections (S2 Table), however, no blowhole swabs of these cases were available.
Microbiological data were considered as unspecific microbiota. Potentially pathogenic bacteria cultured were Clostridium perfringens, Escherichia coli, Klebsiella pneumonia and Vibrio spp., but no associated inflammatory lesions were found histologically. No potential zoonotic organisms such as Brucella spp. and Erysipelothrix rhusiopathiae were isolated.
Previous consumption of squid was evident from large numbers of squid beaks in the gastrointestinal tract, the majority (97%) belonging to the Boreoatlantic armhook squid (Gonatus fabricii). The results of the diet studies reveal that the 13 sperm whales stranded in Germany (ID # 2, 4, 5, 11, 18–25, 27–28) contained 55,150 beaks, representing a cumulative prey biomass of around 12,000 kg; five sperm whales stranded in the Netherlands (ID # 6–10) contained over 11,000 lower beaks, resembling a prey biomass of around 2100 kg; and the one sperm whale that stranded in France contained nearly 33,000 lower beaks, resembling a prey biomass of around 5700 kg. Although there were a high number of squid beaks present in the gastrointestinal tracts of some individuals, they represented non-recent prey consumption, as the majority of the contents mainly consisted of dry squid beaks whilst the prey’s flesh was already digested.
During the period of the strandings, from the end of 2015 through to the beginning of 2016, SST in the northern North Sea was only slightly higher than the average for that time of the year (Table 2, S2 Fig). The ocean currents were predominantly directing from west to east (Table 2), and this was therefore unlikely related to the sperm whale strandings.
One earthquake with a magnitude of 4.5 on Richter scale occurred on 18-12-2015 at 18:29:29.6 UTC, 284 km W of Lisbon, Portugal (39.58N;12.22W). Given its location in the southern North Atlantic Ocean, this was also unlikely to be related to the sperm whale strandings.
Genetics and contamination profiles
Levels of a range of contaminants were determined, but were not considered to be of significance in terms of causality of the mortality event (details in ). Data on contaminant profiles together with genetic data gave evidence for at least two cohorts among the stranded sperm whales with different origins; one from the Canary Islands and one from the northern part of the Atlantic [59,60]. The genetic diversity was comparable to the genetic diversity in sperm whales from the entire Atlantic Ocean and males did not comprise maternally related individuals within this stranding event, but assemblages of individuals from different geographic regions .
A total of 80 sperm whale stranding events were reported in the southern North Sea between 1996 and 2016, comprising 142 individual whales ((S3 Table) excluding Northern Scotland, Orkney and Shetland). Sixteen sperm whales stranded in a single mass stranding event on the Danish Wadden Sea island of Rømø on 27th March 1996. On 4th December 1997 another mass mortality event occurred on the island of Rømø, involving 13 sperm whales. That same year 11 additional sperm whales stranded in eastern Scotland, England, The Netherlands and Germany, making 1996 and 1997 the years with high stranding numbers, followed by 18 years of relatively low stranding numbers, until the mortality event of 2016 (Fig 2).
Here we describe the largest recorded sperm whale mortality event in the southern North Sea, where a total of 27/30 of the stranded sperm whales were necropsied and/or sampled. The cohesive examination of the mortality event across the North Sea region represents the most extensive investigation of a sperm whale mortality event ever undertaken on a global basis. Through the pathological examination, and subsequent ancillary tests, we are able to eliminate poor health status or an identifiable traumatic or infectious disease as the primary driver of this mortality event. Infectious agents, including the novel identified species of herpesvirus, had not impacted the health status of the animals. Marine litter was found in 9/22 sperm whales, but had not caused a functional obstruction and was thus not deemed to be a factor in the death of these animals . Elimination of a deteriorated health status and disease as a common cause of these strandings suggest that other factors, including previously suggested environmental and anthropogenic causes of mass strandings, were plausibly more influential.
Previous mass strandings of beaked whales have been linked to high intensity sources of marine noise, including naval sonar, which probably led to behavioural responses resulting in gas- and fat embolism [17,19]. Cases diagnosed with gas embolism have occasionally been reported in stranded cetaceans from the North Sea region [19,63]. No evidence of significant pathology indicative of gas embolism was found in the fresh sperm whales examined, however it was impossible to assess this for the majority of the stranded sperm whales as they were in an advanced state of decomposition. Additionally the structural analysis of the tympanic bullae of several cases  demonstrated no severe damage. Assessment of the tympanic bullae for any evidence of damage to or loss of the hair cells in the cochlea could not be carried out due to the decomposed condition of the animals.
Anthropogenic acoustic data (e.g. high-intensity naval sonar/activities) and other sources of noise pollution could not be readily assessed in this mortality event. It is impossible to relate acoustic activity to the mortality event as in the North Sea and North East Atlantic an effective register of anthropogenic impulsive noise inputs was lacking. Besides it remains unknown when exactly the sperm whales entered the North Sea or how long they may have been resident there.
Persistent organic pollutants (POPs), particularly polychlorinated biphenyls (PCBs), negatively affect a variety of cetacean species (e.g. ). Levels of a range of potential contaminants were determined in samples collected from sperm whales in this study, but were not deemed to be of significance in terms of direct causality of the stranding event .
Environmental factors that have been proposed to cause mass strandings of cetaceans include harmful algal blooms (HABs, e.g. ) and earthquakes (e.g. ). While there has not been an assessment of exposure to biotoxins from HABs in the sperm whales from this mortality event, this is an unlikely cause of the strandings. The strandings occurred in the middle of the winter, with HABs commonly occurring in the warm-water seasons. Only one earthquake with a magnitude of 4.5 on Richter scale was reported in the southern part of the northern Atlantic Ocean in December 2015. A correlation with the mortality event cannot fully be ruled out, however this seems unlikely as the location of the earthquake was approximately 2500–3000 km away from the northern entrance to the North Sea and occurred three weeks prior to the first stranding event. In addition, and according to the authors’ knowledge, no other increases in sperm whale strandings, or other species, along the east Atlantic coastline have been reported.
Pierce et al.  previously reported a potential relationship between increases in SST and sperm whale stranding rates. This explains 8–9% of the variation in sperm whales strandings in the North Sea. In the period prior to the 2016 strandings, SST of the North Sea was slightly higher than on average for that time of the year. When comparing the SST of years with high and low frequencies of strandings it becomes evident, however, that no obvious trend exists. For the period in 1996, during which a large number of sperm whale strandings was recorded, SST was below the long-term average, whereas in the period before the 2016 strandings, SST was above the average. In years without strandings, we also found no obvious pattern. The potential relationship between climatic variation, including SST, and sperm whale strandings therefore requires further investigation using longer term datasets, to be able to recognize any trends . This should also be done in light of climate change, which may alter prey availability and distribution .
Changes in solar activity have recently been proposed as an explanatory factor for sperm whale stranding events, including those in 2016 . Solar storms can alter the earth’s magnetic field and impact the ability of migratory species to orientate accurately by means of magneto-reception. Vanselow and Ricklefs  showed that between 1712 and 2003 up to 90% of sperm whale strandings occurred during solar cycles of length less than 11 years. We are currently experiencing the end of the 24th solar cycle which began in December 2008 . This solar cycle represents the weakest cycle of the last 115 years , yet it coincides with the largest recorded stranding event of sperm whales in the North Sea. Vanselow et al.  therefore recently moved from investigating entire solar cycles to investigating the relationship between short term solar activity and their potential effects on the earth’s magnetic field. The authors concluded that a single solar storm can shift the magnetic field by up to 460 km for a period of up to a day and may cause sperm whales to deviate from their usual migratory routes into the North Sea and propose this as a possible explanation for the 2016 stranding event. On the other hand preliminary analytical results conducted by NASA in cooperation with the International Fund for Animal Welfare (IFAW) were unable to find any clear causal connection between geomagnetic activity and mass stranding in the vicinity of Cape Cod. However they could not exclude solar weather (or geomagnetic activity) as one of several contributing factors to these events (Personal Communication Katie Moore IFAW). The stranding records for sperm whales in the North Sea represent the longest time series available for any cetacean  and the addition of two decades of further data to the historic database initiated by Smeenk  as presented here, will help facilitate further in-depth analyses regarding this topic.
Sperm whales in the Northeast Atlantic mainly feed on Gonatus fabricii . Similar to previous studies (e.g. [48,71]) all sperm whales had squid beaks in their stomachs. Almost all beaks were identified as G. fabricii, which is distributed throughout the deep and cold waters of Arctic and subarctic regions [70,72]. The southern distribution boundary is around 61° N [73,74]. The main spawning time of G. fabricii depends on the geographical location and occurs between December and February for the area of the eastern Norwegian Sea . Prior to spawning at depth female G. fabricii lose their ability to actively swim as an effect of degeneration of their muscle tissue and subsequently drift in large groups [70,75,76]. This could be used by cetaceans, such as the sperm whale, as an easy-to-access resource . The diet study revealed relatively high (compared to other prey) reconstructed biomass of G. fabricii in the sperm whales’ gastrointestinal tracts, but concluded that the majority of the contents found consisted of dry squid beaks which were not recently ingested. The distance between the southern distribution boundary of G. fabricii and the stranding locations of the sperm whales in the southern North Sea is ~1300 km. Existing records for swimming speeds of sperm whales vary, from 2.9 km/h as a minimum  to 5.4 km/h as a maximum . A sperm whales’ travel time over a distance of ~1300 km would therefore take minimally 10 days (at a speed of 5.4 km/h) and maximally 19 days (at a speed of 2.9 km/h), making it highly likely that these animals had not fed substantially recently, or at least not within the minimal period of 10–19 days prior to their stranding. This also suggests that squid beaks may be retained in sperm whale stomachs for a longer period than previously estimated by Clark  which indicated squid beaks retention times varying from 2.1 to 2.6 days in female sperm whales, to 1.2 to 1.6 days in males.
The North Sea region
Mass mortalities of sperm whales have occurred on the beaches of the (southern) North Sea for centuries. These stranding locations present one common feature: gradually sloping sandy coastlines. The characteristics of the stranding sites are very similar to the characteristics of other stranding sites where mass mortalities involving sperm whales occurred, like along the Italian side of the Adriatic Sea , and in New Zealand and South Australia [26,79]. It has been theorized that strandings of deep diving pelagic cetacean species are centred around such ‘acoustical dead zones’ as a result of distorted echolocation signals due to geometric effects .
It is likely that stranding events in the North Sea have largely been well documented over the past 400 years, providing reasonably accurate stranding records over time. Several periods with relatively large numbers of strandings have been previously identified in 1560–1995 [5,80]. During the 20th century sperm whale mortality events in the North Sea always involved males, primarily immature individuals, which stranded predominantly between November and March ([5,6,21,81], and the CSIP and Naturalis databases; Fig 3). The 2016 mortality event fits into this pattern, with all animals being immature males that stranded in winter. Some historical mortality events stretched over entire winter or spring periods, whereas the event we describe here occurred over a period of only six weeks.
Numbers prior to 1996 derived from Smeenk .
Smeenk  and Evans  described an increase in sperm whale stranding events in the North Sea since the 1970s, and reported through into the 1990s. There has been a general increase in sperm whale strandings around the southern North Sea region over the last ~30 years (S3 Table), with several years of extremely high numbers (1996, 1997 and 2016) and multiple years with low or no strandings (e.g. 1999–2001, 2007–2009). There is a possible relationship between the frequency of strandings and the number of males present at northern latitudes, which might be evidence of some degree of population recovery resulting in an increased number of migrating males . However without accurate population estimates, drawing such assumptions should be treated with caution . Altogether, this emphasises the need for multidisciplinary, cross-boundary, and even cross-region investigations into such mass mortality events and hotspots, especially taking into account changed climatic conditions and increased anthropogenic activities in sperm whale habitats.
In order to elucidate potential reasons for the largest sperm whale stranding event that has ever been recorded in the North Sea we conducted a systematic pathological examination of the majority of the stranded whales, leading to one of the most extensively investigated sperm whale mortality events that has ever taken place. This allowed for a thorough assessment not just into the cause of death and stranding, but also the health of a group of animals almost impossible to study by other means. We are able to eliminate poor health status, any identifiable traumatic event or significant infectious disease process as the primary cause of the 2016 sperm whale strandings. Although all investigated animals had high reconstructed squid biomass in their stomachs we conclude that they did not ingest these recently and not within the North Sea. Whilst the ultimate reason why these animals entered the North Sea remains unknown, and it is impossible to rule out whether these stranding events are just a result of ‘bad luck’ after a navigational fault of (some of) the animals, this was an unprecedented event and enabled a number of potential hypotheses, both natural and man-made, to be excluded. We conclude that no single causal factor for this series of strandings can be identified and it is certainly plausible that a combination of different and coincident factors may have led to this large-scale sperm whale mortality event. A summary of all investigations and their outcomes can be found in S4 Table. It is only through multidisciplinary, collaborative approaches that potentially multifactorial large-scale stranding events can be effectively investigated, and significant causes appointed or excluded.
S1 Table. Overview of pathological findings.
NE = Not Examined. NAD = No Abnormalities Detected. NF = Not Found.
S2 Table. Overview of ancillary diagnostic tests.
Virological, bacteriological and parasitology results of cases investigated. NE = Not Examined. NF = Not Found.
S3 Table. Sperm whale strandings North Sea region.
Overview of all stranded sperm whales along the North Sea coastline (n = 80) from 1997–2016.
S4 Table. Potential drivers of the stranding events, with conclusions on the likelihood of causality for each factor.
Colours reflect whether factors could be excluded (green), were unlikely (light green), or remain uncertain/could not be excluded (orange). In blue the most likely explanation for the stranding events, although the bathymetry of the region does not explain why the animals entered the North Sea.
S1 Fig. Bathymetry of North Sea region and route of sperm whales.
The colour palette represents the total depth of the area, revealing depths of ~500 m in the Faeroe-Shetland channel, depths of approximately 200–400 m in the Norwegian trench, which decrease significantly in the central North Sea to 40 m. Here, sandbanks and coastal areas of 5 m depth are common. The green arrows indicate the route that sperm whales take during their southern migration through the Faeroe-Shetland channel. The red arrow indicates the most likely route sperm whales mistakenly take, by which they enter the North Sea region.
S2 Fig. Sea surface temperature (SST) and sperm whale strandings.
Averaged SST (green line) for the winters with high sperm whales stranding numbers in the North Sea region: 29th of November of the years 1994/95, 1995/96, 1996/97, 1997/98, 2013/14, 2014/15, 2015/16, 2016/17. The dotted line represents the respective confidence interval and the red coloured areas represent the difference of the measured temperature to the long-term. The area between the upper border of the red coloured areas and the green line represents the respective long-term SST average for this period. The blue triangles indicate the exact stranding events of sperm whales for each year in which they occurred.
The Netherlands: The investigations of the event could not have been done without the help of dozens of volunteers, students and researchers (in alphabetic order): Els van Andel, Bart van der Baan, Louis van den Boom, Luuk van den Boom, Elisa Bravo Rebolledo, Camille Chauffray, Coen Cirkel, Arjen Dijkstra, Steve Geelhoed, Amandine Gillet, Bert Meerstra, David van Reenen, Liliane Solé, Martijn Stijntjes, Jesse Thijssen, Naomi Tuhuteru, Hans Verdaat, Simon de Vries. Special thanks to Ecomare and SOS Dolfijn for their coordination during the stranding, to Rijkswaterstaat for their coordination during the necropsy/disposal, and the team of Naturalis for assisting during the necropsy. The necropsies and stomach content analysis were conducted through funding gained from the Dutch Ministry of Economic Affairs (grant number: HD3611/BO11018.02 065).
Germany: The authors thank all helpers for their great efforts during the recovery and necropsy of the sperm whale carcasses in German waters. We would like to thank the Ministry of Energy, Agriculture, the Environment and Rural Areas of Schleswig-Holstein, the State Agency of Coastal Protection, National Parks and Ocean Protection of Schleswig-Holstein as well as the Federal Ministry of the Environment, Nature Conservation, Building and Nuclear Safety for funding the work on the animals in Schleswig-Holstein. Moreover, we owe great thanks for their help to the Water and Shipping Authority Tönning as well as the district veterinarians of Schleswig-Holstein and the State Agency for Agriculture, Environment and Rural Areas Schleswig-Holstein. Similarly our thanks go to the authorities of Lower Saxony, especially the Wadden Sea National Park Authority of Lower Saxony, the Ministry for the Environment, Energy, Construction and Climate Protection of Lower Saxony, and the Lower Saxony State Office for Consumer Protection and Food Safety. Last but not least we thank the Municipality of Wangerooge, the city of Cuxhaven and the Federal Agency for Technical Relief.
England: UK necropsies were conducted by the Cetacean Strandings Investigation Programme, which is funded by Defra and the Devolved Governments of Scotland and Wales. We would like to thank and acknowledge members of the Maritime and Coastguard Agency, East Lindsey District Council, the Le Strange Estate and Kings Lynn and west Norfolk borough council for helping to facilitate the field examinations. We would also like to thank the volunteers of British Divers Marine Life Rescue (particularly Jo Collins, Jane Oxby and Kevin Murphy) and the staff of Hunstanton Sea Life Sanctuary for their assistance during the strandings. Finally, we would particularly like to thank Rod Penrose and Paul Newman for their invaluable help in conducting the examinations and necropsies.
France: We would like to thank and acknowledge the members of the network and students who contributed: For PELAGIS: Demaret Fabien and Dars Cécile, the »CMNF”, « Coordination Mammalogique du Nord de la France”: Jean Luc Bourgain, Clémentine Brévart, Aurélie Dubois, Manon Lefèvre, Julie Mestre and Jacky Karpouzopoulos. For the LPA, « Ligue de Protection des Animaux », Yoan Demassieux and Jérôme Gressier. For « Picardie Nature », Christine Martin. For ULiege, Amandine Gillet and Marianna Pinzone. We also want to thank the speed sail School of Marck Hemmes Sailing for their logistical support during operations on the stranding site and Jérôme Spitz of Universite´ de La Rochelle for making available the stomach contents of the whale that stranded in France.
We would also like to thank Dr. Peter Evans, Mark Delany and an anonymous reviewer for their helpful comments and suggestions during the review process.
- 1. Pyenson ND. The high fidelity of the cetacean stranding record: Insights into measuring diversity by integrating taphonomy and macroecology. Proc R Soc B 2011; 278(1724): 3608–3616. pmid:21525057
- 2. Geraci JR, Lounsbury VR. Marine mammals ashore: A field guide for strandings. 2nd ed. National Aquarium in Baltimore 2005; Baltimore, MD; p 305.
- 3. Whitehead H. Estimates of the current global population size and historical trajectory for sperm whales. Mar Ecol Prog Ser 2002; 242: 295–304.
- 4. Taylor BL, Baird R, Barlow J, Dawson SM, Ford J, Mead JG Physeter macrocephalus. The IUCN Red List of Threatened Species 2008; e.T41755A10554884.
- 5. Smeenk C. Strandings of sperm whales Physeter macrocephalus in the North Sea: history and patterns. Bulletin van het koninklijk Belgisch instituut voor natuurwetenschappen 1997; Bio 67:15–28.
- 6. Pierce GJ, Santos MB, Smeenk C, Saveliev A, Zuur AF. Historical trends in the incidence of strandings of sperm whales (Physeter macrocephalus) on North Sea coasts: An association with positive temperature anomalies. Fish Res 2007; 87: 219–228.
- 7. Steiner L, Lamoni L, Acosta Plata M, Jensen SK, Lettevall E, Gordon JCD. A link between male sperm whales, Physeter macrocephalus, of the Azores and Norway. J Mar Biol Assoc UK 2002; 92(8): 1751–1756.
- 8. Evans PGH. Ecology of sperm whales (Physeter macrocephalus) in the eastern North Atlantic, with special reference to sightings & strandings records from the British Isles. Bulletin De I’Institut Royal Des Sciences Naturelles De Belgique Biologie 1997; 67: 37–46.
- 9. Hansen MS, Alstrup AKO, Hansen JH, Al-Sabi MNS, Nonnemann B, Jensen LF, et al. Stranding of two sperm whales (Physeter macrocephalus) in the "North Sea trap" at Henne Strand, Denmark. Aquat Mamm 2016; 42(1):35–41.
- 10. Walday M, Kroglund T. The North Sea. European Environment Agency 2008; p 32, Copenhagen.
- 11. Camphuysen CJ. Strandings of Sperm Whales Physeter macrocephalus in the NE Atlantic region: a review. Report to the Emergency Response Fund of the United Nations Environmental Programme 1995; CSR Report 1995–3, Oosterend, Texel.
- 12. Jepson PD, Bennet PM, Deaville R, Allchin CR, Baker JR, Law RJ. Relationships between polychlorinated biphenyls and health status in harbor porpoises (Phocoena phocoena) stranded in the United Kingdom. Environ Toxicol Chem 2005; 24: 238–248. pmid:15683190
- 13. Siebert U, Wünschmann A, Weiss R, Frank H, Benke H, Frese K. Post mortem findings in harbour porpoises (Phocoena phocoena) from the German North and Baltic Sea. J Comp Pathol 2001; 124: 102–114. pmid:11222006
- 14. Jauniaux T, Hartmann GM, Haelters J, Tavernier J, Coignoul F. Echouage de mammife`res marins: guide d’intervention et procedures d’autopsie. Ann. Me´d. Ve´t 2002; 146: 261–276.
- 15. Jepson PD, Bennett PM, Allchin CR, Law RJ, Kuiken T, Baker JR, et al. Investigating potential associations between chronic exposure to polychlorinated biphenyls and infectious disease mortality in harbour porpoises from England and Wales. Sci Total Environ 1999; 243: 339–348. pmid:10635603
- 16. Beineke A, Siebert U, MacLachlan M, Bruhn R, Thron K, Failing K, Müller G, Baumgärtner W. Investigations of the potential influence of environmental contaminants on the thymus and spleen of harbor porpoises (Phocoena phocoena). Environ Sci Technol 2005; 39: 3933–3938. pmid:15984767
- 17. Fernández A, Edwards JF, Rodriguez F, De Los Monteros AE, Herraez P, Castro P. Gas and fat embolic syndrome involving a mass stranding of beaked whales (family Ziphiidae) exposed to anthropogenic sonar signals. Vet Path 2005; 42(4): 446–457.
- 18. Das K, Vossen A, Tolley K, Vikingsson G, Thron K, Müller G, Baumgärtner W, Siebert U. Interfollicular fibrosis on the thyroid glands of the harbour porpoise (Phocoena phocoena): An endocrine disruption? Arch Environ Contam Toxicol 2006; 51: 720–729. pmid:16465558
- 19. Jepson PD, Arbelo M, Deaville R, Patterson IAP, Castro P, Baker JR, et al. Gas-bubble lesions in stranded cetaceans. Nature 2003; 425: 575–576. pmid:14534575
- 20. Jepson PD, Deaville R, Barber JL, Aguilar À, Borrell A, Murphy S, et al. PCB pollution continues to impact populations of orcas and other dolphins in European waters. Sci Rep 2016; 6:18573. pmid:26766430
- 21. Jauniaux T, Brosens L, Jacquinet E, Lambrigts D, Addink M, Smeenk C, Coignoul F. Postmortem investigations on winter stranded sperm whales from the coasts of Belgium and The Netherlands. J Wildl Dis 1998; 34:99–109. pmid:9476231
- 22. Vanselow KH, Ricklefs K. Are solar activity and sperm whale Physeter macrocephalus strandings around the North Sea related? J Sea Res 2005; 53: 319–327.
- 23. Wright A. Lunar cycles and sperm whales (Physeter macrocephalus) strandings on the North Atlantic coastlines of the British isles and eastern Canada. Mar Mamm Sci 2005; 21: 145–149.
- 24. Evans K, Thresher R, Warneke RM, Bradshaw CJ, Pook M, Thiele D, Hindell MA. Periodic variability in cetacean strandings: links to large-scale climate events. Biol Lett 2005; 1:147–150. pmid:17148151
- 25. Jacobsen JK, Massey L, Gulland F. Fatal ingestion of floating net debris by two sperm whales (Physeter macrocephalus). Mar Pollut Bull 2010; 60(5): 765–767. pmid:20381092
- 26. Mazzariol S, Di Guardo G, Petrella A, Marsili L, Fossi CM, Leonzio C, et al. Sometimes sperm whales (Physeter macrocephalus) cannot find their way back to high seas: A multidisciplinary study on a mass stranding. PLoS ONE 2011; 6(5):e19417. pmid:21673789
- 27. Squadrone S, Chiaravalle E, Gavinelli S, Monaco G, Rizzi M, Abete MC. Analysis of mercury and methylmercury concentrations, and selenium: mercury molar ratios for a toxicological assessment of sperm whales (Physeter macrocephalus) in the most recent stranding event along the Adriatic coast (Southern Italy, Mediterranean Sea). Chemosphere 2015; 138: 633–41. pmid:26233668
- 28. Cools P, Haelters J, dos Santos Santiago GL, Claeys G, Boelens J, Leroux-Roels I. Edwardsiella tarda sepsis in a live-stranded sperm whale (Physeter macrocephalus). Vet Microbiol 2013; 166(1–2): 311–315. pmid:23827352
- 29. Mazzariol S, Centelleghe C, Di Provvido A, Di Renzo L, Cardeti G, Cersini A, et al. Dolphin Morbillivirus associated with a mass stranding of sperm whales, Italy. Emerg Infect Dis 2017;23(1):144–146. pmid:27983493
- 30. Kuiken T, Garcia Hartmann M (eds). Proceedings of the first European Cetacean Society workshop on cetacean pathology: dissection techniques and tissue sampling. ECS newsletter 17, 1993; Special issue, p 39
- 31. Deaville R, Jepson PD (compilers), UK Cetacean Strandings Investigation Programme Final report for the period 1st January 2005-31st December 2010. 2011; http://randd.defra.gov.uk/Document.aspx?Document=FinalCSIPReport2005-201.
- 32. Evans K, Hindell MA, Robertson K, Lockyer C, Rice D. Factors affecting the precision of age determination of sperm whales (Physeter macrocephalus). J Cetacean Res Manage 2002; 4(2): 193–201.
- 33. Lehnert K, Raga JA, Siebert U. Macroparasites in stranded and bycaught harbour porpoises from German and Norwegian waters. Dis Aquat Organ 2005; 64: 265–269. pmid:15997825
- 34. Lambertsen R. Natural disease problems of the sperm whale. Bulletin de l’Institut Royal des Sciences Naturelles de Belgique Biologie 1997; 67: 105–112.
- 35. Agusti C, Aznar FJ, Olson PD, Littlewood DTJ, Kostadinova A, Raga JA. Morphological and molecular characterization of tetraphyllidean merocercoids (Platyhelminthes: Cestoda) of striped dolphins (Stenella coeruleoalba) from the Western Mediterranean. J Parasitol 2005; 130(04): 461–474.
- 36. Hall T. BioEdit: a user-friendly biological sequence alignment editor and analysis program for Windows 95/98/NT. Nucleic Acids Symposium Series 1999; 41: 95–98. Retrieved from http://jwbrown.mbio.ncsu.edu/JWB/papers/1999Hall1.pdf
- 37. Tamura K, Dudley J, Nei M, Kumar S. MEGA4: Molecular Evolutionary Genetics Analysis (MEGA) Software Version 4.0. Mol Biol Evol 2007; 24(8): 1596–1599. pmid:17488738
- 38. Benson DA, Karsch-Mizrachi I, Lipman DJ, Ostell J, Wheeler DL. GenBank. Nucleic Acids Research, 33(Database issue) 2005; D34–D38. pmid:15608212
- 39. Siebert U, Prenger-Berrninghof E, Weiss R. Regional differences in bacteria flora in harbour porpoises from the North Atlantic: environmental effects. J Appl Microbiol 2009; 106: 329–337. pmid:19120613
- 40. Prenger-Berninghoff E, Siebert U, Stede M, Weiß R. Incidence of Brucella species in marine mammals of the German North Sea. Dis Aquat Organ 2008; 81(1), 65–71. pmid:18828563
- 41. Munster VJ, Baas C, Lexmond P, Waldenström J, Wallensten A, Fransson T, et al. Spatial, temporal, and species variation in prevalence of Influenza A viruses in wild migratory birds. PLoS Pathog 2007; 3(5): e61. pmid:17500589
- 42. Barrett T, Visser IKG, Mamaev L, Goatley L, Van Bressem MF, Osterhaus ADME. Dolphin and porpoise morbilliviruses are genetically distinct from phocine distemper virus. Virol 1993; 193(2): 1010–1012.
- 43. VanDevanter DR, Warrener P, Bennett L, Schultz ER, Coulter S, Garber RL, Rose TM. Detection and Analysis of Diverse Herpesviral Species by Consensus Primer PCR. J Clin Microbiol 1996; 34 (7): 1666–71. pmid:8784566
- 44. Seki F, Ono N, Yamaguchi R, Yanagi Y. Efficient isolation of wild strains of Canine distemper virus in Vero cells expressing canine SLAM (CD150) and their adaptebility to Marmoset B95a cells. J Virol 2003; 77(18): 9943–9950. pmid:12941904
- 45. Katoh K, Standley DM. MAFFT Multiple Sequence Alignment Software Version 7: Improvements in Performance and Usability. Mol Biol Evol 2013; 30(4): 772–780. pmid:23329690
- 46. Schnitzler JG, Frédérich B, Früchtnicht S, Schaffeld T, Baltzer J, Ruser A, Siebert U. Size and shape variations of the bony components of sperm whale cochleae. Sci Rep 2017; 7: 46734. pmid:28440286
- 47. Morell M, Lenoir M, Shadwick RE, Jauniaux T, Dabin W, Begeman L, et al. Ultrastructure of the Odontocete organ of Corti: scanning and transmission electron microscopy. J Comp Neurol 2015; 523(3): 431–48. pmid:25269663
- 48. Santos MB, Pierce GJ, Boyle PR, Reid RJ, Ross HM, Patterson IAP, et al. Stomach contents of sperm whales Physeter macrocephalus stranded in the North Sea 1990–1996. Mar Ecol Prog Ser 1999; 183: 281–294.
- 49. Unger B, Bravo Rebolledo EL, Deavile R, Grone A, IJsseldijk LL, Leopold MF, et al. Large amounts of marine debris found in sperm whales stranded along the North Sea coast in early 2016. Mar Pol Bul 2016; 112(1–2): 134–141.
- 50. Rebolledo EL, IJsseldijk LL, Solé L, Begeman L, De Vries S, Van Den Boom L. et al. Unorthodox sampling of a fin Whale’s (Balaenoptera physalus) diet yields several new mesopelagic prey species. Aquat Mamm 2016; 42(4): 417.
- 51. Clarke MR. Cephalopoda in the diet of sperm whales of the southern hemisphere and their bearing on sperm whale biology. 1980; Vol. 37, University Press.
- 52. Clarke MR. A Handbook for the Identification of Cephalopod Beaks. Clarendon Press 1986; 273 pages.
- 53. EMSC. European-Mediterranean Seismological Centre. 2017; https://www.emsc-csem.org/Earthquake/?filter=yes (accessed 09-09-2017)
- 54. Reynolds RW, Smith TM, Liu C, Chelton DB, Casey KS, Schlax MG. Daily High-Resolution-Blended Analyses for Sea Surface Temperature. J Clim 2007; 20(22): 5473–5496.
- 55. R Core Team. R: A language and environment for statistical computing. R Foundation for Statistical Computing, Vienna, Austria. 2017; URL https://www.R-project.org/
- 56. Hijmans RJ. Raster: Geographic Data Analysis and Modeling. R package version 2.6–7. 2017; https://CRAN.R-project.org/package=raster
- 57. Pebesma EJ, Bivand RS. Classes and methods for spatial data in R. R News 5 (2), https://cran.r-project.org/doc/Rnews/., Roger S. Bivand, Edzer Pebesma, Virgilio Gomez-Rubio, 2013. Applied spatial data analysis with R 2005; Second edition, Springer, New York. http://www.asdar-book.org/
- 58. Pierce D. ncdf4: Interface to Unidata netCDF (Version 4 or Earlier) Format Data Files. R package version 1.16, 2017. https://CRAN.R-project.org/package=ncdf4
- 59. Autenrieth M, Ernst A, Deaville R, Demaret F, IJsseldijk LL, Siebert U, Tiedemann R. Putative origin and maternal relatedness of male sperm whales (Physeter macrocephalus) recently stranded in the North Sea. Mamm Biol 2017; 88: 156–160.
- 60. Schnitzler JG, Pinzone M, Autenrieth M, van Neer A, IJsseldijk LL, et al. Inter-individual differences in contamination profiles as tracer of social group association in stranded Sperm whales. Sci Rep 2018; 8: 10958. pmid:30026609
- 61. EMODnet Bathymetry Consortium. EMODnet Digital Bathymetry (DTM). EMODnet Bathymetry 2016; http://doi.org/10.12770/c7b53704-999d-4721-b1a3-04ec60c87238
- 62. George JC, Philo LM, Hazard K, Withrow D, Carroll GM, Suydam R. Frequency of Killer Whale (Orcinus orca) Attacks and ship collisions based on scarring on Bowhead whales (Balaena mysticetus) of the Bering-Chukchi-Beaufort Seas stock. Arctic 1994; 247–255.
- 63. Siebert U, Jepson PD, Wohlsein P. First indication of gas embolism in a harbour porpoise (Phocoena phocoena) from German waters. Eur J Wildl Res 2013; 59(3): 441–444.
- 64. Fire SE, Wang Z, Byrd M, Whitehead HR, Paternoster J, Morton SL. Co-occurrence of multiple classes of harmful algal toxins in bottlenose dolphins (Tursiops truncatus) stranding during an unusual mortality event in Texas, USA. Harmful Algae 2011; 10(3): 330–336.
- 65. Bradshaw CJ, Evans K, Hindell MA. Mass cetacean strandings: a plea for empiricism. Conserv Bio 2006; 584–586.
- 66. Learmonth JA, MacLeod CD, Santos MB, Pierce GJ, Crick HQP, Robinson RA. Potential effects of climate change on marine mammals. Oceanogr Mar Biol 2006; 44: 431.
- 67. Vanselow KH, Jacobsen S, Hall C, Garthe S. Solar storms may trigger sperm whale strandings: explanation approaches for multiple strandings in the North Sea in 2016. Int J Astrobiol 2017; 1–9.
- 68. Brajša R, Verbanac G, Sudar D, Skokić I, Žic T, Hanslmeier A, et al. A comparison between the observed and predicted amplitude of the 24th solar cycle. Central European Astrophysical Bulletin 2015; 39: 135–144.
- 69. Tlatov AG, Pevtsov AA. On the timing of the next great solar activity minimum. Adv Space Res 2017; 1610.
- 70. Bjørke H, Gjøsæter H. Cephalopods in the Norwegian Sea. In The Norwegian Sea Ecosystem, pp. 371–394. Ed. by Skjoldal HR. Tapir Academic Press 2004; Trondheim, 559 pp.
- 71. Santos MB, Pierce GJ, Hartmann MG, Smeenk C, Addink MJ, Kuiken T, et al. Additional notes on stomach contents of sperm whales Physeter macrocephalus stranded in the north-east Atlantic. Journal of the Mar Biol Assoc UK 2002; 82(3): S0025315402005787.
- 72. Piatkowski U, Zumholz K, Jereb P, Seixas S, Oesterwind D, Lefkaditou E, et al. Gonatus fabricii (Lichtenstein, 1818). In: Cephalopod biology and fisheries in Europe 2015: II. Species Accounts, ed. by Jereb P, Allcock L, Lefkaditou E, Piatkowski U, Hastie LC and Pierce GJ, ICES Coop Res Rep 325, ICES, Copenhagen, Denmark, pp. 229–238.
- 73. Wiborg KF, Gjøsæter J, Beck IM. The squid Gonatus fabricii (Lichtenstein): Investigations in the Norwegian Sea and western Barents Sea 1978–1981. 1982; Bergen, Norway: ICES. Retrieved from https://brage.bibsys.no/xmlui/handle/11250/102062
- 74. Wiborg KF, Gjøsæter J, Beck, IM. The squid Gonatus fabricii (Lichtenstein): Investigations in the Norwegian Sea and western Barents Sea 1982–1983. 1984; Bergen, Norway: ICES. Retrieved from https://brage.bibsys.no/xmlui/handle/11250/102064
- 75. Arkhipkin AI, Bjørke H. Ontogenetic changes in morphometric and reproductive indices of the squid Gonatus fabricii (Oegopsida, Gonatidae) in the Norwegian Sea. Polar Biol 1999, 22(6): 357–365.
- 76. Bjørke H, Hansen K. Recordings of mature Gonatus fabricii (Lichtenstein) off the Norwegian coast. 1996; Bergen, Norway: ICES. Retrieved from https://brage.bibsys.no/xmlui/handle/11250/105633
- 77. Watkins WA, Daher MA, Fristrup KM, Howald TJ, di Sciara GN. Sperm whales tagged with transponders and tracked underwater by sonar. Mar Mamm Sci 1993, 9(1): 55–67.
- 78. Miller PJO, Johnson MP, Tyack PL, Terray EA. Swimming gaits, passive drag and buoyancy of diving sperm whales Physeter macrocephalus. J Exp Biol 2004; 207: 1953–1967. pmid:15107448
- 79. Sundaram B, Poje AC, Veit RR, Nganguia H. Acoustical dead zones and the spatial aggregation of whale strandings. J Theor Biol 2006; 238: 764–770. pmid:16083913
- 80. Smeenk C, Camphuysen CJ. Potvis Physeter macrocephalus. In: Broekhuizen S, K Spoelstra, JBM Thissen, KJ Canters, JC Buys (eds). Atlas van de Nederlandse Zoogdieren. Natuur van Nederland 12, Naturalis Biodiversity Center, Eis Kenniscentrum insecten en andere ongewervelden, Zoogdiervereniging en KNNV Uitgeverij, 2016; Zeist, p 320–325, The Netherlands.
- 81. Berrow SD, Evans PGH, Sheldrick ML. An analysis of sperm whale Physeter microcephalus stranding and sighting records, from Britain to Ireland. J Zool Lond 1993; 230, 333–337.
- 82. Evans PGH. Ecology of Sperm Whales (Physeter macrocephalus) in the Eastern North Atlantic, with special reference to sightings and strandings records from the British Isles. Pp. 37–46. In: Sperm Whale Deaths in the North Sea Science and Management (Editors Thierry G. Jacques and Richard H. Lambertsen). Bull. de L’Institut Royal des Sciences Naturelles de Belgique. Biologie 1997; 67, 133pp.