Genetic monitoring

Genetic monitoring is the use of molecular markers to (i) identify individuals, species or populations, or (ii) to quantify changes in population genetic metrics (such as effective population size, genetic diversity and population size) over time. Genetic monitoring can thus be used to detect changes in species abundance and/or diversity, and has become an important tool in both conservation and livestock management. The types of molecular markers used to monitor populations are most commonly mitochondrial, microsatellites or single-nucleotide polymorphisms (SNPs), while earlier studies also used allozyme data. Species gene diversity is also recognized as an important biodiversity metric for implementation of the Convention on Biological Diversity.[1]

Types

Types of population changes that can be detected by genetic monitoring include population growth and decline, spread of pathogens, adaptation to environmental change, hybridization, introgression and habitat fragmentation events. Most of these changes are monitored using ‘neutral’ genetic markers (markers for which mutational changes do not change their adaptive fitness within a population). However markers showing adaptive responses to environmental change can be ‘non-neutral’ (e.g. mutational changes affect their relative fitness within a population).

Categories of Genetic Monitoring as defined by Schwartz et al. 2007[2]

Two broad categories of genetic monitoring have been defined:[2] Category I encompasses the use of genetic markers as identifiers of individuals (Category Ia), populations and species (Category Ib) for traditional population monitoring. Category II represents the use of genetic markers to monitor changes of population genetic parameters, which include estimators of effective population size (Ne), genetic variation, population inter-mixing, structure and migration.

Examples

Estimating abundance and life history parameters – Category Ia

At the individual level, genetic identification can enable estimation of population abundance and population increase rates within the framework of mark-recapture models. The abundance of cryptic or elusive species that are difficult to monitor can be estimated by collecting non-invasive biological samples in the field (e.g. feathers, scat or fur) and using these to identify individuals through microsatellite or single-nucleotide polymorphism (SNP) genotyping. This census of individuals can then be used to estimate population abundance via mark-recapture analysis. For example, this technique has been used to monitor populations of grizzly bear,[3] brush-tailed rock-wallaby,[4] Bengal tiger[5] and snow leopard.[6] Population growth rates are a product of rates of population recruitment and survival, and can be estimated through open mark-recapture models. For example, DNA from feathers shed by the eastern imperial eagle shows lower cumulative survival over time than seen for other long-lived raptors.[7]

Identifying species – Category Ib

Use of molecular genetic techniques to identify species can be useful for a number of reasons. Species identification in the wild can be used to detect changes in population ranges or site occupancy, rates of hybridization and the emergence and spread of pathogens and invasive species. Changes in population ranges have been investigated for Iberian lynx[8] and wolverine,[9] while monitoring of westslope cutthroat trout shows widespread ongoing hybridization with introduced rainbow trout [10] (see cutbow) and Canada lynx-bobcat hybrids have been detected at the southern periphery of the current population range for lynx.[11][12] The emergence and spread of pathogens can be tracked using diagnostic molecular assays – for example, identifying the spread of West Nile virus among mosquitoes in the eastern US to identify likely geographical origins of infection[13] and identifying gene loci associated with parasite susceptibility in bighorn sheep.[14] Genetic monitoring of invasive species is of conservation and economic interest, as invasions often affect the ecology and range of native species and may also bring risks of hybridization (e.g. for copepods,[15] ducks,[16] barred owl and spotted owl,[17] and Lessepsian rabbitfish[18]).

Species identification is also of considerable utility in monitoring fisheries and wildlife trade, where conventional visual identification of butchered or flensed products is difficult or impossible.[19] Monitoring of trade and consumption of species of conservation interest can be carried out using molecular amplification and identification of meat or fish obtained from markets. For example, genetic market surveys have been used to identify protected species and populations of whale (e.g., North Pacific minke whale) and dolphin species appearing in the marketplace.[20] Other surveys of market trade have focused on pinnipeds,[21] sea horses[22] and sharks.[23] Such surveys are used to provide ongoing monitoring of the quantity and movement of fisheries and wildlife products through markets and for detecting poaching or other illegal, unreported or unregulated (IUU) exploitation [19] (e.g. IUU fishing).

Although initial applications focused on species identification and population assessments, market surveys also provide the opportunity for a range of molecular ecology investigations including capture-recapture, assignment tests and population modeling.[19] These developments are potentially relevant to genetic monitoring Category II.

Monitoring population genetic parameters – Category II

Monitoring of population changes through genetic means can be done retrospectively, through analysis of 'historical' DNA recovered from museum-archived species and comparison with contemporary DNA of that species. It can also be used as a tool for evaluating ongoing changes in the status and persistence of current populations. Genetic measures of relative population change include changes in diversity (e.g. heterozygosity and allelic richness). Monitoring of relative population changes through these metrics has been performed retrospectively for Beringian bison,[24] Galapagos tortoise,[25] houting,[26] Atlantic salmon,[27] northern pike,[28] New Zealand snapper,[29] steelhead trout,[30] greater prairie chicken,[31] Mauritius kestrel[32] and Hector's dolphin[33] and is the subject of many ongoing studies, including Danish and Swedish brown trout populations.[34][35] Measuring absolute population changes (e.g. effective population size (Ne)) can be carried out by measuring changes in population allele frequencies (‘Ftemporal’) or levels of linkage disequilibrium over time (‘LDNe’), while changing patterns of gene flow between populations can also be monitored by estimating differences in allele frequencies between populations over time. Subjects of such studies include grizzly bears,[3][36][37] cod,[38] red deer,[39] Leopard frogs[40] and Barrel Medic.[41][42]

Genetic monitoring has also been increasingly used in studies that monitor environmental changes through changes in the frequency of adaptively selected markers. For example, the genetically controlled photo-periodic response (hibernating time) of pitcher-plant mosquitos (Wyeomyia smithii) has shifted in response to longer growing seasons for pitcher plants brought on by warmer weather.[43] Experimental wheat populations grown in contrasting environments over a period of 12 generations found that changes in flowering time were closely correlated with regulatory changes in one gene, suggesting a pathway for genetic adaptation to changing climate in plants.[44][45]

Genetic monitoring is also useful in monitoring the ongoing health of small, relocated populations. Good examples of this are found for New Zealand birds, many species of which were greatly impacted by habitat destruction and the appearance of numerous mammalian predators in the last century and have recently become part of relocation programs that transfer a few ‘founder’ individuals to predator-free offshore “ecological” islands. E.g. black robin,[46] and kakapo.[47]

Status of genetic monitoring in science

In February 2007 an international summit was held at the Institute of the Environment at UCLA, concerning ‘Evolutionary Change in Human Altered Environments: An International Summit to translate Science into Policy’. This led to a special issue of the journal of Molecular Ecology[48] organized around our understanding of genetic effects in three main categories: (i) habitat disturbance and climate change (ii) exploitation and captive breeding (iii) invasive species and pathogens.

In 2007 a Working Group on Genetic Monitoring was launched with joint support from NCEAS[49] and NESCent[50] to further develop the techniques involved and provide general monitoring guidance for policy makers and managers.[51]

Currently the topic is covered in several well known text books, including McComb et al. (2010) and Allendorf et al. (2013)

Genetic monitoring in natural resource agencies

Many natural resource agencies see genetic monitoring as a cost-effective and defensible way to monitor fish and wildlife populations. As such scientists in the U.S. Geological Survey, U.S. Forest Service,[52] National Park Service, and National Marine Fisheries Service have been developing new methods and tools to use genetic monitoring, and applying such tools across broad geographic scales.[2][36] Currently the USFWS hosts a website that informs managers as to the best way to use genetic tools for monitoring (see below).

See also

References

  1. ↑ Website of the Convention on Biological Diversity
  2. 1 2 3 Schwartz, M.K., et al. (2007) Genetic monitoring as a promising tool for conservation and management. Trends Ecol. Evol. 22, 25–33. doi:10.1016/j.tree.2006.08.009PDF fulltext
  3. 1 2 Boulanger, J., et al. (2004) Monitoring of grizzly bear population trends and demography using DNA mark-recapture methods in the Owikeno Lake area of British Columbia. Canadian Journal of Zoology 82, 1267–1277. doi:10.1139/Z04-100
  4. ↑ Piggott, M.P., et al. (2006) Estimating population size of endangered Brush-tailed Rock-wallaby (Petrogale penicillata) colonies using faecal DNA. Mol. Ecol. 15, 81–91. doi:10.1111/j.1365-294X.2005.02783.x
  5. ↑ Bhagavatula, J., and Singh, L. (2006) Genotyping faecal samples of Bengal tiger Panthera tigris tigris for population estimation: A pilot study. BMC Genet. 7, 48. doi:10.1186/1471-2156-7-48
  6. ↑ Jaňecka, J.E., et al. (2008) Population monitoring of snow leopards using noninvasive collection of scat samples: a pilot study. Anim. Conserv. 11, 401–411. doi:10.1111/j.1469-1795.2008.00195.x
  7. ↑ Rudnick, J.A., et al. (2005) Using naturally shed feathers for individual identification, genetic parentage analyses, and population monitoring in an endangered Eastern imperial eagle (Aquila heliaca) population from Kazakhstan. Mol. Ecol. 14, 2959–2967. doi:10.1111/j.1365-294X.2005.02641.x
  8. ↑ Fernández, N., et al. (2006) Landscape evaluation in conservation: molecular sampling and habitat modeling for the Iberian lynx. Ecol. Appl. 16, 1037–1049. doi:10.1890/1051-0761(2006)016[1037:LEICMS]2.0.CO;2
  9. ↑ Schwartz, M.K., et al. (2007) Inferring geographical isolation of wolverines in California using historical DNA. J. Wildl. Manage. 71, 2170–2179. doi:10.2193/2007-026PDF fulltext
  10. ↑ Hitt, N.P., et al. (2003) Spread of hybridization between native westslope cutthroat trout, Oncorhynchus clarki lewisi, and nonnative rainbow trout, Oncorhynchus mykiss. Can. J. Fish. Aquat. Sci. 60, 1440–1451. doi:10.1139/F03-125
  11. ↑ Homyack, J.A., et al. (2008) Canada lynx-bobcat (Lynx canadensis x L.rufus) hybrids at the southern periphery of lynx range in Maine, Minnesota and New Brunswick. Am. Midl. Nat. 159, 504–508. doi:10.1674/0003-0031(2008)159[504:CLLCLR]2.0.CO;2PDF fulltext
  12. ↑ Schwartz, M.K., et al. (2004) Hybridization between Canada lynx and bobcats: Genetic results and management implications. Conserv. Genet. 5, 349–355.doi:10.1023/B:COGE.0000031141.47148.8bPDF fulltext
  13. ↑ Kilpatrick, A.M., et al. (2006) West Nile Virus epidemics in North America are driven by shifts in mosquito feeding behavior. PLoS Biol. 4, 606–610. doi:10.1371/journal.pbio.0040082PDF fulltext
  14. ↑ Luikart, G., et al. (2008) Candidate gene microsatellite variation is associated with parasitism in wild bighorn sheep. Biol. Lett. 4, 228–231. doi:10.1098/rsbl.2007.0633PDF fulltext
  15. ↑ Lee, C.E. (1999) Rapid and repeated invasions of fresh water by the copepod Eurytemora affinis. Evolution 53, 1423–1434. PDF fulltext
  16. ↑ Seyoum, S; Tringali, MD; Bielefeld, RR; Feddersen, JC; Benedict Jr, RJ; Fanning, AT; Barthel, B; Curtis, C; Puchulutegui, C; Roberts, ACM; Villanova Jr, VL; Tucker, EC (2012). "Fifty-nine microsatellite markers for hybrid classification studies involving endemic Florida Mottled Duck (Anas fulvigula fulvigula) and invasive Mallards (A. platyrhynchos)". Conservation Genetics Resources. 4 (3). doi:10.1007/s12686-012-9622-9.
  17. ↑ Haig, S.M., et al. (2004) Genetic identification of spotted owls, barred owls and their hybrids: legal implications of hybrid identity. Conserv. Biol. 18, 1347–1357. doi:10.1111/j.1523-1739.2004.00206.x
  18. ↑ Azzurro, E., et al. (2006) Genetics of the early stages of invasion of the Lessepsian rabbitfish Siganus luridus. J. Exp. Mar. Biol. Ecol. 333, 190–201. doi:10.1016/j.jembe.2005.12.002 PDF fulltext
  19. 1 2 3 Baker, C.S. (2008) A truer measure of the market: the molecular ecology of fisheries and wildlife trade. Mol. Ecol. 17, 3985–3998. doi:10.1111/j.1365-294X.2008.03867.x
  20. ↑ Baker, C.S., et al. (2007) Estimating the number of whales entering trade using DNA profiling and capture-recapture analysis of market products. Mol. Ecol. 16, 2617–2626. doi:10.1111/j.1365-294X.2007.03317.x
  21. ↑ Malik, S., et al. (1997) Pinniped penises in trade: a molecular genetic investigation. Conserv. Biol. 11, 1365–1374. doi:10.1046/j.1523-1739.1997.96125.x
  22. ↑ Sanders, J.G., et al. (2008) The tip of the tail: molecular identification of seahorses for sale in apothecary shops and curio stores in California. Conserv. Genet. 9, 65–71. doi:10.1007/s10592-007-9308-0
  23. ↑ Clarke, S.C., et al. (2006) Identification of shark species composition and proportion in the Hong Kong shark fin market based on molecular genetics and trade records. Conserv. Biol. 20, 201–211. doi:10.1111/j.1523-1739.2005.00247.x
  24. ↑ Shapiro, B., et al. (2004) Rise and fall of the Beringian Steppe Bison. Science 306, 1561–1565. doi:10.1126/science.1101074 PMID 15567864 PDF fulltext
  25. ↑ Poulakakis, N., et al. (2008) Historical DNA analysis reveals living descendants of an extinct species of Galápagos tortoise. Proc. Natl. Acad. Sci. USA 105, 15464–15469. doi:10.1073/pnas.0805340105PDF fulltext
  26. ↑ Hansen, M.M., et al. (2006) Underwater but not out of sight: genetic monitoring of effective population size in the endangered North Sea houting (Coregonus oxyrhynchus). Can. J. Fish. Aquat. Sci. 63, 780–787. doi:10.1139/F05-260
  27. ↑ Nielsen, E.E., et al. (1999) Genetic variation in time and space: Microsatellite analysis of extinct and extant populations of Atlantic salmon. Evolution 53, 261–268.
  28. ↑ Miller, L.M., and Kapuscinski, A.R. (1997) Historical analysis of genetic variation reveals low effective population size in a northern pike (Esox lucius) population. Genetics 147, 1249–1258. PDF fulltext
  29. ↑ Hauser, L., et al. (2002) Loss of microsatellite diversity and low effective population size in an overexploited population of New Zealand snapper (Pagrus auratus). Proc. Natl. Acad. Sci. USA 99, 11742–11747. doi:10.1073/pnas.172242899 PDF fulltext
  30. ↑ Heath, D.D., et al. (2002) Temporal change in genetic structure and effective population size in steelhead trout (Oncorhynchus mykiss). Mol. Ecol. 11, 197–214. doi:10.1046/j.1365-294X.2002.01434.x
  31. ↑ Bellinger, M.R. (2003) Loss of genetic variation in greater prairie chickens following a population bottleneck in Wisconsin, USA. Conserv. Biol. 17, 717–724. doi:10.1046/j.1523-1739.2003.01581.x
  32. ↑ Groombridge, J.J., et al. (2000) 'Ghost' alleles of the Mauritius kestrel. Nature 403, 616. doi:10.1038/35001148
  33. ↑ Pichler, F.B., and Baker, C.S. (2000) Loss of genetic diversity in the endemic Hector's dolphin due to fisheries-related mortality. Proc. R. Soc. Lond., Ser. B: Biol. Sci. 267, 97–102. doi:10.1098/rspb.2000.0972 PDF fulltext
  34. ↑ Østergaard, S., et al. (2003) Long-term temporal changes of genetic composition in brown trout (Salmo trutta L.) populations inhabiting an unstable environment. Mol. Ecol. 12, 3123–3135. doi:10.1046/j.1365-294X.2003.01976.x
  35. ↑ Palm, S., et al. (2003) Effective population size and temporal genetic change in stream resident brown trout (Salmo trutta, L.). Conserv. Genet. 4, 249–264. doi:10.1023/A:1024064913094
  36. 1 2 Kendall, K.C., et al. (2009) Demography and genetic structure of a recovering grizzly bear population. J. Wildl. Manage. 73, 3–17. doi:10.2193/2008-330
  37. ↑ Proctor, M.F., et al. (2005) Genetic analysis reveals demographic fragmentation of grizzly bears yielding vulnerably small populations. Proc. R. Soc. Lond., Ser. B: Biol. Sci. 272, 2409–2416. doi:10.1098/rspb.2005.3246 PMID 16243699 PDF fulltext
  38. ↑ Poulsen, N.A., et al. (2006) Long-term stability and effective population size in North Sea and Baltic Sea cod (Gadus morhua). Mol. Ecol. 15, 321–331. doi:10.1111/j.1365-294X.2005.02777.x
  39. ↑ Nussey, D.H., et al. (2005) Rapidly declining fine-scale spatial genetic structure in female red deer. Mol. Ecol. 14, 3395–3405. doi:10.1111/j.1365-294X.2005.02692.xPDF fulltext
  40. ↑ Hoffman, E.A., and Blouin, M.S. (2004) Historical data refute recent range contraction as cause of low genetic diversity in isolated frog populations. Mol. Ecol. 13, 271–276. doi:10.1046/j.1365-294X.2003.02057.xPDF fulltext
  41. ↑ Bonnin, I., et al. (2001) Spatial effects and rare outcrossing events in Medicago truncatula (Fabaceae). Mol. Ecol. 10, 1371–1383. doi:10.1046/j.1365-294X.2001.01278.x
  42. ↑ Siol, M., et al. (2007) Effective population size associated with self-fertilization: lessons from temporal changes in allele frequencies in the selfing annual Medicago truncatula. J. Evol. Biol. 20, 2349–2360 doi:10.1111/j.1420-9101.2007.01409.x
  43. ↑ Bradshaw, W.E., and Holzapfel, C.M. (2001) Genetic shift in photoperiodic response correlated with global warming. Proc. Natl. Acad. Sci. USA 98, 14509–14511. doi:10.1073/pnas.241391498 PDF fulltext
  44. ↑ Rhoné, B., et al. (2008) Insight into the genetic bases of climatic adaptation in experimentally evolving wheat populations. Mol. Ecol. 17, 930–943. doi:10.1111/j.1365-294X.2007.03619.x
  45. ↑ Strasburg, J.L., and Gross, B.L. (2008) Adapting to winter in wheat: a long-term study follows parallel phenotypic and genetic changes in three experimental wheat populations. Mol. Ecol. 17, 716–718. doi:10.1111/j.1365-294X.2007.03639.x
  46. ↑ Ardern, S.L., and Lambert, D.M. (1997) Is the black robin in genetic peril? Mol. Ecol. 6, 21–28. doi:10.1046/j.1365-294X.1997.00147.x
  47. ↑ Miller, H.C., et al. (2003) Minisatellite DNA profiling detects lineages and parentage in endangered kakapo (Strigops habroptilus) despite low microsatellite DNA variation. Conserv. Genet. 4, 265–274. doi:10.1023/A:1024037601708
  48. ↑ A Report on the Results and Recommendations of the International Summit on Evolutionary Change in Human-altered Environments
  49. ↑ National Center for Ecological Analysis and Synthesis
  50. ↑ The National Evolutionary Synthesis Center
  51. ↑ Genetic Monitoring: Development of Tools for Conservation and Management
  52. ↑ Rocky Mountain Research Station Wildlife Genetics Laboratory

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