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Study area
We conducted our study at Nopporo Forest Park in Hokkaido, Japan (43° 03′ N, 141° 32′ E) (Fig. 1). This forest is a semi-isolated 2,053 ha area surrounded by residential areas and farmland. There have been concerns about raccoon impacts on this ecosystem since they were first detected in 199234.
Animals
We captured raccoons using box traps (Havahart Large Collapsible Pro Cage Model 1089, Woodstream Corp., Lititz, PA, USA) from May to July in 2018 and April to August in 2019. Traps were placed at 86 sites (Fig. 1). Trapping points within 250 m of the forest boundary line facing the farmland were defined as ‘around the farmland’ (31 points), and other points were defined as ‘in the forest’ (55 points) using QGIS version 3.1023. Captured raccoons were anesthetised with butorphanol tartrate (Vetorphale 5 mg, 1.2 mg/kg; Meiji Seika, Tokyo, Japan), medetomidine hydrochloride (Dolbene, 40 µg/kg; Kyoritsu, Tokyo, Japan), and midazolam (Dormicum injection 10 mg, 0.2 mg/kg; Astellas, Tokyo, Japan) by intramuscular injection and euthanised by potassium chloride injection into the heart. We captured 48 raccoons (34 around the farmland, 14 in the forest) in 2018, and 27 (12 around the farmland, 15 in the forest) in 2019 (Fig. 1). We collected thigh muscle samples, rectal faeces, and gastric contents from captured raccoons. Samples were stored at − 20 °C until analysis.
DNA metabarcoding
Sample preparation
Rectal faeces and gastric contents that were dominated by plant materials and groomed hair were excluded from analyses. In total, 18 rectal faeces and six gastric content samples that contained animal materials or whose contents were unknown were selected. Rapidly digested food resources such as amphibians cannot be confirmed visually in gastrointestinal contents, and even DNA may not be detected. Therefore, multiple samples were pooled and analysed because the target DNA may not be detected otherwise. The rectal faeces and gastric contents were divided into five (S1–S5) and two groups (G1–G2), respectively, based on the capture site and date of raccoons (Table 1). Each group was mixed and stored at − 20 °C until DNA extraction. Subsequent DNA analyses were performed at Bioengineering Lab. Co., Ltd. (Kanagawa, Japan).
DNA extraction
Samples (about 100 mg each) were lyophilised using a VD-250R lyophiliser freeze dryer (TAITEC, Saitama, Japan) and ground using a ShakeMaster NEO homogeniser (Bio Medical Science, Tokyo, Japan). Crude DNA was extracted from each group; then, DNA was purified using the MPure-12 Automated Nucleic Acid Purification System (MP Biomedicals, California, USA) with a MPure Bacterial DNA Extraction Kit (MP Biomedicals).
Library preparation and sequencing
Each library was prepared using two-step tailed PCR. We used the gSalamander primer, which amplifies salamander and newt 12S rRNA, as a specific primer to detect Hokkaido salamander, and the gInsect primer, which amplifies arthropod 16S rRNA, to detect Japanese crayfish (Table 5). All primers were designed by Bioengineering Lab. Co., Ltd.
Table 5 Primer sets used in this study.
Full size table

The first PCR amplified the target region using gSalamander and gInsect. These reactions were conducted in a final volume of 10 μl, comprising 2 μl DNA template, 0.5 μl each primer (10 μM), 0.1 μl Ex Taq HS (5 U/µl) (Takara Bio Inc., Shiga, Japan), 1.0 μl 10 × Ex Taq buffer, 0.8 μl dNTP mixture (2.5 mM), and 5.1 μl sterile distilled water. The PCR conditions were: first denaturation for 2 min at 94 °C, followed by 35 cycles of 30 s at 94 °C, 30 s at 50 °C, and 30 s at 72 °C, and final extension for 5 min at 72 °C.
The second PCR used the first PCR products as the template with index primers (2ndF and 2ndR). These reactions were conducted in a final volume of 10 μl, as described for the first PCR. The PCR conditions were: first denaturation for 2 min at 94 °C, followed by 12 cycles of 30 s at 94 °C, 30 s at 60 °C, and 30 s at 72 °C, and final extension for 5 min at 72 °C. At each step, PCR products were purified using the Agencourt AMPure XP system (Beckman Coulter, Inc., California, USA). The library concentrations were measured with a Synergy H1 microplate reader (BioTek) and a QuantiFluor dsDNA System (Promega). Library quality was assessed using a Fragment Analyser (Advanced Analytical Technologies, Iowa, USA) with a dsDNA 915 Reagent Kit (Agilent, California, USA). Paired-end sequencing (2 × 300 bp) was conducted on the Illumina MiSeq platform (Illumina, California, USA).
Data analysis
Reads that began with a sequence that completely matched the primer used were extracted using the fastq_barcode_splitter tool in the FASTX-Toolkit; then, the primer sequence was trimmed. The reads were trimmed and filtered using the Sickle tool with a quality value of 20; then, trimmed and paired-end reads with fewer than 150 bases were discarded. The remaining reads were merged using the FLASH paired-end merge script35 under the following conditions: fragment length after merge, 300 bases; read fragment length, 230 bases; and minimum overlap length, 10 bases. The UCHIME2 algorithm within USEARCH was used to check all filtered sequences for chimeric sequences36. All sequences that were not judged to be chimeras were used for further analysis. The UPARSE algorithm within USEARCH was used for OTU creation and taxonomic assignments. The constructed OTUs were subjected to Basic Local Alignment Search Tool (BLASTN) searches. More than 100 reads and the top BLAST hit with a sequence identity of ≥ 97% were used to assign species (target length: about 300 bp) to each representative sequence37.
Additional analyses of COI region
S–2, S–3, G–1, and G–2 sample group DNA was successfully extracted using gSalamander or gInsect primers (Table 1) and analysed by PCR using COI and blocking primers for raccoon (Table 5). The library was prepared using two-step tailed PCR. The first PCR amplification using the primer set 1st-IntF and 1st-HCOmR was conducted in a final volume of 10 μl, comprising 2 μl DNA template, 5 μl of each primer (10 μM) (forward primer 0.5 µl, reverse primer 0.5 µl, blocking primer 4 µl), 0.08 μl Ex Taq HS (5 U/µl), 1.0 μl 10 × Ex Taq buffer, 0.8 μl dNTP mixture (2.5 mM), and 1.12 μl DDW. The PCR conditions were as follows: first denaturation for 2 min at 94 °C, followed by 35 cycles of 30 s at 94 °C, 15 s at 67 °C, and 30 s at 52 °C and 30 s at 72 °C, and final extension for 5 min at 72 °C. Subsequent methods were as described above, except for the FLASH paired-end merge script (fragment length after merge, 310 bases; read fragment length, 225 bases).
Stable isotope analysis
Stable isotope ratios of muscle tissue reflect the diet over the previous few weeks to one month38,39. We used the muscles of raccoons captured from April to August and assumed that the stable isotope ratios in raccoon muscle samples reflected their diet from March to July, i.e. late winter to early summer, in Hokkaido.
Raccoon muscle and potential prey item samples were dried at 60 °C for  > 24 h and then ground with a mortar and pestle. Potential food items (such as amphibians and crustaceans) were collected from the forest. The raccoon muscle and potential prey item samples were rinsed with a 2:1 chloroform: methanol solution to remove lipids and then dried at 60 °C for at least 24 h40. Each sample (1.0–3.0 mg) was enclosed in a tin cup and combusted in an elemental analyser (Vario MICRO cube, Elementar Gmbh, Hanau, Germany) interfaced with an isotope ratio mass spectrometer (IsoPrime100, Elementar Gmbh). We determined the δ13C, δ15N, and δ34S values for each sample. The results are reported as parts per thousand of the isotopes relative to a standard. For δ13C, δ15N, and δ34S values, Vienna Pee Dee Belemnite, air, and Vienna Cañon Diablo Triolite were used as standards, respectively. We used L-alanine (Shoko Science Co., Ltd., Tokyo, Japan) and sulfanilamide (Elementar GmbH) as working standards. A working standard, sulfanilamide (δ34S value, − 1.92‰), was calibrated against IAEA (International Atomic Energy Agency, Vienna, Austria) silver sulfides, IAEA-S-1, IAEA-S-2, IAEA-S-3, and was used as a working standard for δ34S.
Statistical analysis
We performed two-way analysis of variance to examine the interactions between two independent variables, season (spring: April–June vs. summer: July–August) and capture site (around the farmland vs. in the forest), and their relationship with the dependent variables (stable isotope ratio; δ13C, δ15N, and δ34S). After examining interactions between two independent variables (season and capture site), a Mann–Whitney U test was conducted. Differences were considered statistically significant at P  More

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To the Editor — A wildlife consumption ban, which China enacted in February as a response to the COVID-19 pandemic, has been welcomed by most conservationists as a step towards avoiding a future outbreak of zoonotic diseases1. There are dissenting voices against this ban, arguing that wildlife generates multiple benefits for people who co-exist with wild species2. While both schools of thought have their own valid arguments, neither has yet to actively lobby for the free, prior and informed consent or consultation of the people who will be directly affected by conservation decisions related to COVID-19.

Throughout the years, indigenous peoples and local communities (IPLCs) have been seen as either culprits of biodiversity decline or as ‘unseen sentinels’ effectively managing and monitoring their territories, which are often highly biodiverse3. This polarized view of IPLCs signals a prevailing lack of understanding of their way of life, where most of their dependence on nature is on a subsistence level. Wildlife consumption is often an essential part of their diets. A blanket ban on wildlife consumption may, therefore, exacerbate food insecurity in these communities. In other cases, IPLC wildlife consumption is more than just for subsistence. It may also have cultural roots and should be respected in that regard. Calling for education campaigns to ‘discredit engrained cultural beliefs’ that lead to wildlife consumption ignores the dynamics of cultural development and would most likely fail to conserve wildlife or fail to prevent another zoonotic disease outbreak4. What is needed is to craft bottom-up solutions together with the IPLCs directly depending on wildlife and to learn from their nuanced understanding of nature.

Through creating opportunities and spaces for dialogue, governments and institutions can involve IPLCs in setting guidelines for wildlife consumption. They can adopt the dialogue approach employed by the Intergovernmental Science-Policy Platform on Biodiversity and Ecosystem Services (IPBES), where IPLCs engage in knowledge exchange with technical experts and government representatives5. The dialogue, through parallel contributions of indigenous, local, scientific and practical knowledge, can enhance the understanding of wildlife consumption6. Governments and institutions can tap into the network of non-governmental organizations (NGOs) that closely collaborate with IPLCs and have them facilitate these dialogues. They need to listen carefully to IPLCs, learn from their customary protocols on wildlife use and consumption, and draft laws that could potentially prevent another zoonotic disease outbreak without jeopardizing the livelihoods and well-being of IPLCs. Likewise, IPLCs and civil society can continue to build on processes of self-strengthening and assert themselves in spaces where they can proactively engage in efforts to raise awareness and understanding of traditional wildlife consumption practices. These multiple stakeholders must work together to co-craft potential solutions to this global yet also very local concern of wildlife consumption and its connection to zoonotic diseases.

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Affiliations

Center for Development Research (ZEF) Bonn, University of Bonn, Bonn, Germany
Denise Margaret S. Matias

Institute for Social-Ecological Research (ISOE), Frankfurt am Main, Germany
Denise Margaret S. Matias

Non-Timber Forest Products Exchange Programme (NTFP-EP) Asia, Quezon City, Philippines
Eufemia Felisa Pinto & Diana San Jose

Non-Timber Forest Products Exchange Programme (NTFP-EP) India, c/o Keystone Foundation, Kotagiri, India
Madhu Ramnath

Authors
Denise Margaret S. Matias

Eufemia Felisa Pinto

Madhu Ramnath

Diana San Jose

Contributions
D.M.S.M. conceptualized and drafted the Correspondence. E.F.P. and D.S.J. provided input. M.R. reviewed the Correspondence.
Corresponding author
Correspondence to Denise Margaret S. Matias.

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Competing interests
The authors declare no competing interests.

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Matias, D.M.S., Pinto, E.F., Ramnath, M. et al. Local communities and wildlife consumption bans. Nat Sustain (2020). https://doi.org/10.1038/s41893-020-00662-7
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