Characterization of six microsatellite loci in Myrica faya (Myricaceae) and cross amplification in the endangered endemic M. rivas-martinezii in Canary Islands, Spain

ABSTRACT

GENETICS

Characterization of six microsatellite loci in Myrica faya (Myricaceae) and cross amplification in the endangered endemic M. rivas-martinezii in Canary Islands, Spain

Miguel A. González-Pérez¹

Craig Newton²

Pedro A. Sosa¹

Elizabeth Rivero¹

Edna A. González-González¹

¹Departamento de Biología, Universidad de Las Palmas de Gran Canaria, Canary Islands, Spain

²ATG Genetics Inc, Vancouver, British Columbia, Canada

Six novel polymorphic microsatellite markers were isolated from enriched libraries in Myrica faya Ait., recently renamed Morella faya, (fayatree, firetree, or firebush) in order to examine the genetic diversity in natural populations. Also, test cross-specific amplification and genetic diversity in Myrica rivas-martinezii, which is endemic on the Canary islands. Microsatellite loci were screened in 225 individuals of both species from different islands of the Canarian archipelago. All markers were successfully amplified from both Myrica species, with an average number of 6.5 and 9.3 alleles per locus in M. rivas-martinezii and M. faya, respectively. There was no evidence for linkage disequilibrium between loci, and the probability of null alleles ranged from 0.01 to 0.17.

M. faya co-occurs very close (separated by few meters) to Myrica rivas-martinezii A. Santos. The latter is an endangered endemic species of the laurel forests on the Canary Islands. M. rivas-martinezii is found on rather poor soils along the inferior margins of the laurel forest domain, especially in isolated locations that have been the object of multiple exploitations. It is a perennial, woody species that was first time described in El Hierro in 1980 (^{Santos-Guerra, 1980}). This dioecious tree species occurs on only three islands (El Hierro, La Gomera and La Palma) of the Canarian archipelago. Its most abundant population (with about 40 individuals) is located at El Fayal, in an area of approximately 90 km² on El Hierro Island. Only ten isolated individuals are known in La Gomera Island, six of which have male flowers, all in different locations and separated by linear distances ranging from 1 to 7 km, but isolated by deep ravines and cliffs. In La Palma, the only two known individuals (one male and one female) are separated by more than 20 km (^{Bañares et al., 2004}). Myrica rivas-martinezii has been classified as Critically Endangered according to IUCN categories (^{VVAA, 2000}). It is also protected by the Canarian Government (^{Boletín Oficial de Canarias – BOC, 2001}) and the European Habitat Directive (Beltrán et al., 1999).

Previous studies showed no evidence for genetic differentiation on the basis of the sequences of either the pastid rbcl gene, which encodes the large subunit of rubisco, or the 18S-26S nuclear internal transcribed spacer (ITS) region (^{Huguet et al., 2005}). Yet, ^{Batista et al. (2004)} showed higher genetic diversity levels in M. rivas-martinezii using RAPDs.

We sampled 41 specimens of Myrica rivas-martinezii and 183 of M. faya in El Hierro, La Gomera, and La Palma Island (Table 1). Microsatellite loci were isolated from M. faya genomic DNA using biotin/streptavidin enrichment (^{Khasa et al., 2000}). Briefly, genomic DNA was digested with restriction endonucleases (HaeIII, AluI and RsaI) and linkers were added using T4 DNA ligase. Linker adapted total genomic fragments were then enriched by hybridization with 5' biotin AC₁₂ and TC₁₂ followed by separation with streptavidin paramagnetic beads (M270S, Invitrogen, CA). After amplification with linker-specific primers, enriched fragments were cloned into plasmid vectors (pGEM3Z+, Promega) and single colonies containing ACn or TCn microsatellites were identified by colony hybridisation. After one round of biotin enrichment, 75/1000 ampicillin resistant colonies contained microsatellite sequences. Inserts from 23 positive colonies were amplified with M13 universal forward and reverse primers, treated with exonuclease I and Antarctic alkaline phosphatase (New England Biolabs) , and then sequenced from both orientations using a ABI3730 capillary electrophoresis system (NAPS Service, University of British Columbia).

PCR primers complementary to the flanking regions of 13 loci were designed with approximately 40% GC and avoiding palindromic sequence motifs. Out of 13 microsatellite loci analyzed, six yielded PCR products of expected size and were considered robust and predictable enough for further analyses (Table 2).

Total DNA was extracted following the ^{Dellaporta et al. (1983)} method modified by ^{Corniquel and Mercier (1994)}. Each 25 μL PCR reaction contained approximately 20 ng DNA, 10 pmol of each primer, 0.25 μL BSA (0.4%), as well as PCR Master Mix (Reddy-Mix, ABgene, Surrey, UK). Amplifications were carried out using the following conditions: 3 min denaturation at 95 °C, 35 cycles of 30 s denaturation at 95 °C, 30 s. annealing at 55 °C, and 1.5 min elongation at 72 °C, followed by 5 min final elongation at 72 °C. The products were detected using an ABI 3100 Genetic Analyzer and fragment sizes were determined using GENESCAN v. 2.02 and GENOTYPER v. 1.1 (Applied Biosystems, Inc.). We identified allele peak profiles at each locus and assigned a genotype to each individual.

Exact Hardy-Weinberg tests to measure the significance of deviations from the null hypothesis of random union of gametes (^{Guo and Thompson, 1992}) were carried out on natural populations of M. rivas-martinezii and M. faya using Fisher exact test, both for each pair of loci and within each population using GENEPOP 1.2. (^{Raymond and Rousset, 1995}). Basic genetic diversity indices, mean number of alleles (A), the observed (Ho), and unbiased expected (He) heterozygosities (^{Nei, 1978}), paternity exclusion probability (Q) (^{Weir, 1996}), and probability of genetic identity (I) (^{Paetkau et al., 1995}), were estimated using IDENTITY 1.0. The combined probability of paternity exclusion, QC = 1 - [Π(1 – Q_i)] and the combined probability of genetic identity IC = ΠI_i were also estimated for overall loci. The proportion of null alleles for each locus was calculated as (He-Ho)/1 +He, following ^{Brookfield (1996)}.

All six loci were polymorphic, the number of alleles ranging from 3 (M24) to 16 (M10), while Ho ranged from 0.30 (M5) to 0.88 (M10), and gene diversity (He) from 0.32 (M5) to 0.89 (M10). Only one locus (M24) showed values of proportion of null alleles over 10% in both species, suggesting the possibility of null alleles (Table 2). Except for locus M24, none of the other loci showed significant deviations from Hardy-Weinberg equilibrium in M. rivas-martinezii, (data not shown). The M24 locus was estimated to have a null allele frequency of 0.16.

While there was no evidence for linkage disequilibrium between loci in the data set of 225 individuals of both Myrica species, three (M11, M20 and M24) of the six analyzed loci showed significant defect of heterozygote in M. faya. These three loci were estimated to have null allele frequencies of 0.10, 0.04, and 0.17, respectively. Many of the loci showed high probability of paternity exclusion, which should provide powerful markers for paternity exclusion when genotype data from several loci are combined. Total paternity exclusion probability (QC) for this set of six microsatellite loci was estimated at 0.981 for M. faya, and 0.941 for M. rivas-martinezii. Total probabilities of identity (IC) were 5.7110^-6 and 9.0310^-5 for M. faya and M. rivas-martinezii, respectively.

Genetic diversity recorded for the endemic species M. rivas-martinezii was similar to those described for other endangered endemic species of the Canary Islands, for example Bencomia exstipulata (A = 6.20, Ho = 0.43, He = 0.65) (^{González-Pérez et al., 2004}). In contrast genetic variability in M. faya was higher than corresponding values detected in other, not endangered native species of the Canary Islands, e.g., B. caudata (A = 6.40, Ho = 0.47, He = 0.62) (González-Pérez et al., 2004). This may reflect the high colonizing capacity of M. faya (^{Bañares et al., 2004}).

Altogether, the primers described in this paper can provide useful markers to investigate genetic relationship between Myrica rivas-martinezii and M. faya.

Acknowledgments

We thank Angel Fernandez and Cito Chinea (Garajonay National Park), and Eduardo Carqué and Manuel Marrero (Teide National Park) for assistance in collecting Myrica samples. This work was supported by Ministerio de Educación y Ciencia, Dirección General de Investigación, Plan Nacional de I+D+I (CGL2004-03839). Edna A. González-González work was supported by a fellowship for Ministerio de Asuntos Exteriores y Cooperación-Agencia Española de Cooperación Internacional. We also thank Javier Sosa and Andrew Stephens for the revision of the English in this manuscript.

References

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Internet Resources

Boletin Oficial de CanariasDecreto 151, de 23 de julio, por el que se crea el catalogo de especies amenazadas de Canarias. Boletin Oficial de Canarias 97:11101-11111. (2001) Available from: http://www.gobiernodecanarias.org/boc/2001/097/004.html

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Table 1
- Myrica rivas-martinezii and M. faya populations analysed in the Canary Islands.

N = sample size.

Table 2
- Characteristics of six microsatellite loci developed for Myrica faya and cross amplification in M. rivas-martinezii. Number of alleles (A), observed heterozygosity (Ho), expected heterozygosity (He), probability of paternity exclusion (Q), probability of genetic identity (I), proportion of null alleles (Pna), and GenBank accession number.

Received: February 7, 2008; Accepted: June 3, 2008

Miguel Angel González-Pérez. Departamento de Biología, Universidad de Las Palmas de Gran Canaria, Campus Universitario de Tafira 35017, Las Palmas de Gran Canaria, Canary Islands, Spain. E-mail: [e-mail].

M. faya is native to the northern islands of Macaronesia, the Azores, Madeira, and the Canaries in the North Atlantic Ocean. It is found in most laurel forest plots, but also grows well at degraded sites and outside the range of the laurel forest ecosystems. M. faya is quite abundant due to its high colonizing capacity (^{Bañares et al., 2004}). In addition, Myrica faya has been recognized as one of the twelve most noxious plants alien to Hawaii due to its ability to rapidly and aggressively invade and colonize the Hawaiian environment (^{Smith, 1985}).

Tables

Associate Editor: Márcio de Castro Silva Filho

Publication Dates

• Publication in this collection
  10 Jan 2009
• Date of issue
  2009

History

• Accepted
  3062
• Received
  7022