| Citation: |
Ernesto C. Rodríguez-Ramírez, Levinn Camacho-Islas, Ana Paola Martínez-Falcón, Isolda Luna-Vega, Pilar Carbó-Ramírez. 2021: Masting effect on alpha and beta avian diversity in fragmented forests of relict-endangered Mexican Beech (Fagus grandifolia subsp. mexicana). Avian Research, 12(1): 49. DOI: 10.1186/s40657-021-00284-3
|
Tropical montane cloud forests are one of the most important hotspots on Earth and show presence of relict-endemic and endangered species, representing about 14% of the total tropical forest worldwide. Synchronous seed production or masting in tropical montane cloud tree species is a widespread reproductive strategy of deciduous and evergreen broad-leaved tree associations to decrease costs of reproduction and ensure offspring. Masting event maintains a high avian diversity, which can be modified by phenological process (seed production and non-seed production).
The main aim of this study was to assess alpha and beta avian diversity and whether the composition of the trophic guild modifies among phenological processes and between two fragmented relict-endangered Mexican Beech (Fagus grandifolia subsp. mexicana) forests (Medio Monte and El Gosco) in the Mexican state of Hidalgo. In addition, we evaluated beechnut production.
We recorded 36 bird species, 11 of them included in some conservation risk status, and 5 endemic species. Alpha diversity values were dissimilar in avian richness (q=0) among phenological processes and between fragmented beech forests. Avian communities among three phenological processes and between fragmented forests were structurally similar, dominated during immature seeds the Brown-backed Solitaire (granivores–insectivores–frugivores); during mature seeds the White-crowned Parrot (Pionus senilis, granivores–frugivores); and the Dwarf Jay (Cyanolyca nana, insectivores) was abundant during low seed quality. The complementarity index was high among phenological processes and low between forests. We found a high bird turnover value between immature seeds—mature seeds and during mature seeds—low seed quality. Furthermore, a similar pattern was recorded between the two study forests. Seed production showed a high number of undamaged beechnuts in Medio Monte, while in El Gosco beechnuts were attacked by insects.
Our results reflect that masting phenological process and contrasting study forests' structure influence the shifts in alpha and beta diversity of seed and non-seed bird consumers. Our study reaffirms the importance of continuing studies throughout masting in all the Mexican Beech forests to address regional efforts in preserving the relict-ecological interactions.
The Eurasian Collared Dove (Streptopelia decaocto) is a kind of bird classified in the pigeon family Columbidae, and is morphologically the same in both sexes. The Eurasian Collared Dove is not a migratory bird but is strongly dispersed and widely distributed throughout the world (Smith 1987; Romagosa and McEneaney 1999; Owen 2005; Brazil 2009; Gill and Donsker 2019). The country of origin is thought to be India (Del Hoyo et al. 1997), and today it is mainly distributed on the Eurasian continent and North Africa (Smith 1987; Fujisaki et al. 2010). Molecular phylogenetic analysis reports that it is closely related to African Collared Dove (Streptopelia roseogrise; Johnson et al. 2001).
In Japan, the Eurasian Collared Dove is thought to have been introduced artificially from India in the 16th century (The Ornithological Society of Japan 2012) and it inhabits part of the Kanto region (Saitama, Chiba, Ibaraki and Gunma prefectures). As a result of a survey on the population of Eurasian Collared Doves in Saitama Prefecture conducted in 1968, it was estimated that there were 700 individuals in maximum (Kuroda 1969). In 1980, the estimated population was reported to be 10, 000 (Saitama Prefecture 1982). However, the population has been decreasing since then, and it was reported that it estimates from 46 to 68 individuals in the 2008 population survey (Konita et al. 2011). Population surveys have continued since then, but the population remains at double digits (Saitama Prefecture web site). The decrease in the number of Eurasian Collared Dove is thought to be due to the destruction of habitats, the decrease in the number of poultry houses that feed, and the thorough control of poultry houses entry (Saitama Prefecture 2013). For this reason, the Eurasian Collared Dove is designated as endangered IB (EN) by the Japanese Ministry of the Environment's Red List and is protected (Japanese Ministry of the Environment 2014). The low population size of this species raises concerns about reduced genetic diversity. Assessment of the genetic diversity of this species is an urgent task because it is essential to increase genetic diversity as well as population size in order to protect the species at risk. The genetic diversity of the Eurasian Collared Dove in Pakistan and European countries has already been reported using the Cytochrome c oxidase (COI) gene (Awan et al. 2013; Bagi et al. 2018). In this study, to understand the genetic differences between the wild population and the zoo-bred population in Japan, we extracted DNA from the wild population and samples collected from zoos in Saitama Prefecture, and performed analysis by sequencing and comparing mitochondrial DNA (mtDNA).
A total of 19 feather samples of the Eurasian Collared Dove used in the present study were collected from the field at seven locations in Saitama Prefecture, Japan, and another 20 feathers were collected from individuals at five zoos in Saitama Prefecture, Japan (Fig. 1). One eggshell of the Eurasian Collared Dove was also obtained from the field in Saitama Prefecture. Wild samples were collected from nests or from the ground within a 3-4 m radius from just under the nests, and only one sample was collected from each nest to avoid duplication of the same individual. Seven samples were collected in Kuki, six collected in Kawashima, two in Kasukabe and Misato, and one in Kounosu, Satte, and Saitama, respectively. From the zoo, one to nine feather samples were obtained from five zoos. A Ringneck Dove (Streptopelia risoria) sample was also collected from the zoo. All samples were collected between 2017 and 2019, and were sheltered from the sun immediately after collection and were frozen to avoid DNA degradation.
DNA was extracted from the feathers through the spin-column method (NucleoSpin Tissue Kit; MACHEREY–NAGEL, Düren, Germany). The feathers containing soft tissues were cut into small pieces using sterilized scissors, placed in 200 μL of DNA extraction buffer and incubated overnight at 56 ℃, resulting to an eluted final volume of 50 μL. For the eggshell sample, the inside of the eggshell was wiped with a cotton swab soaked in DNA extraction buffer and incubated. A partial mtDNA fragment of COI and the Control Region (CR) was amplified through polymerase chain reaction (PCR) using the following primers specifically designed for this study; Sd-COI-F (5′-GTGACCCTAATCAATCGATG-3′) and Sd-COI-R2 (5′-TATGTAGCCGAAGGGTTC-3′) were used for COI, and SD-CR-F15665 (5′-CCCTGCATCTGTGTCCTATG-3′) and SD-CR-R3 (5′-CATTATTAATGGTTTGTCAGCGG-3′) were used for CR, respectively. The mtDNA control region has been widely applied to the population genetics of various animal species including birds because its mutation rate is approximately 2.8–5 times faster than other sequence segments (Avise et al. 1987; Nagata et al. 1998; Avise 2000).
Each amplification process was conducted using a reaction mixture of 20 μL containing 1 μL template DNA, 10 mM deoxynucleotides (2.5 mM each), 5 nM of each primer, 2 μL buffer, and 1 U of Ex Taq polymerase (TaKaRa, Shiga, Japan). The thermal cycling conditions involved an initial denaturation step at 94 ℃ for 5 min, 45 cycles of denaturation at 95 ℃ for 10 s, annealing at 57 ℃ for COI and 62 ℃ for CR for 30 s, elongation at 72 ℃ for 60 s, and final elongation at 72 ℃ for 2 min. The PCR products were confirmed by 2% agarose gel electrophoresis and purified using Nucleo Spin Gel and PCR Clean-up kit (MACHEREY–NAGEL). The purified product was eluted with 20 μL elution buffer. All the amplified fragments were sequenced with both forward and reverse primers. The PCR products were used as the template for the 10-μL cycle sequencing reactions using BigDye Terminator v3.1 Cycle Sequencing Kit (Applied Biosystems, Foster City, CA, USA). The sequences were generated using a four-capillary 3500 Genetic Analyzer (Applied Biosystems) and the specific primer.
Multiple sequence alignment was then performed using CLUSTAL W (Thompson et al. 1994). The sequence waveform data were checked manually to avoid mistakes due to sequence reactions. Haplotype and nucleotide diversities were calculated based on the 1140-bp fragment of the CR using DnaSP version 6.12 (Rozas et al. 2017). The haplotype network was constructed using TCS 1.21 (Clement et al. 2000). The mtDNA CR sequences were deposited in the DNA Data Bank of Japan (DDBJ), European Molecular Biology Laboratory (EMBL), and GenBank under the accession numbers LC529745–LC529747, and LC530631, respectively.
Mismatch distribution analysis (Rogers and Harpending 1998) was performed with DnaSP 6 and Arlequin 3.5 (Excoffier and Lischer 2010) to test for signatures of recent population expansion. DnaSP 6 was used to develop figures and Arlequin 3.5 was used to calculate the values. Tajima's D (Tajima 1983) and Fu's FS tests (Fu 1997) of selective neutrality were performed using Arlequin 3.5. Negative Tajima's D values suggest that a population has recently increased in size. The fit to a sudden expansion model was judged using the value of the sum of squared deviations (SSD). The lack of significant differences in the SSD values indicated that the population assumed an expansion model. The Harpending's raggedness index (rg) was used to distinguish between expanded and stationary populations with the observed mismatched distributions (Harpending et al. 1993). The value of rg is typically low and inconsequential in expanding populations but high and significant in stationary populations (Harpending 1994). The phylogenetic relationships among the sequences were traced through the maximum likelihood (ML) method (Yang 1994) with MEGA 7 software (Kumar et al. 2016). The ML analysis was performed using the GTR + I + G model. The model was selected with the highest parameter of maximum likelihood fits using the Find Best-Fit Substitution Model of MEGA 7. A closely related S. chinensis and S. orientalis sample (DDBJ/EMBL/NCBI Accession number: KP636801 and NC031447) were used as the outgroup and the previously reported mtDNA of Chinese Eurasian Collared Dove was used for analysis in this study (KX372273). Their corresponding CR sequences were aligned for the phylogenetic analysis.
In this study, we determined a total of 1918 bp of mtDNA from a total of 40 wild and zoo-reared individuals: 778 bp of the COI gene and 1140 bp of the CR. The 778 bp of the COI gene was the same sequence in all 40 individuals, and no mutation sites could be confirmed. In the CR, two base substitution sites were confirmed in 1140 bp, they were transitions, and neither transversion nor indel was confirmed. In the wild, three haplotypes were detected in 20 individuals, whereas all 20 zoo individuals possessed the same haplotype (Table 1). SD-A, SD-B, and SD-C were detected in 6, 11, and 3 individuals, respectively, indicating that SD-B was the major haplotype in wild populations. All zoo animals possessed SD-A.
| Location | Number | Haplotype ID | |||
| A | B | C | |||
| Wild | Kounosu | 1 | 1 | ||
| Saitama | 1 | 1 | |||
| Satte | 1 | 1 | |||
| Kasukabe | 2 | 1 | 1 | ||
| Misato | 2 | 1 | 1 | ||
| Kuki | 7 | 7 | |||
| Kawashima | 6 | 2 | 3 | 1 | |
| Total | 20 | 6 | 11 | 3 | |
| Zoo | A | 1 | 1 | ||
| B | 2 | 2 | |||
| C | 9 | 9 | |||
| D | 6 | 6 | |||
| E | 2 | 2 | |||
| Total | 20 | 20 | |||
| The number in parenthesis represents the number of samples. Column indicates haplotype ID number | |||||
DownLoad:
CSV
Phylogenetic analysis based on the obtained sequences showed that the three haplotypes of Eurasian Collared Dove were clustered, and the sequences of Eurasian Collared Dove from China registered in the NCBI database were identical to those of SD-A (Fig. 2). Phylogenetic analysis using CR showed conventional phylogenetic relationships (Johnson et al. 2001). The results of network analysis showed a star-shape formed by a single base difference centered on SD-A, and showed a difference of 9 bases from Ringneck Dove (Fig. 3).
The haplotype diversity of the wild individual was 0.616 ± 0.077, and the nucleotide diversity was 0.00077 (Table 2). The mismatch distribution analysis for wild showed a unimodal shape (Fig. 4). The SSD value of the wild did not have significant difference. In the selective neutrality test, Tajima's D and Fu's FS were neither significantly different.
| Specimen | n | Haplotype | Variable site | Haplotype diversity | Nucleotide diversity | Tajima's D | Fu's FS | SSD | rg | τ |
| Wild | 20 | 3 | 2 | 0.616 ± 0.077 | 0.00077 | 0.93886 | 0.69483 | 0.00556 | 0.10557 | 0.961 |
| Zoo | 20 | 1 | 0 | 0 | 0 | – | – | – | – |
DownLoad:
CSV
This study revealed that wild Eurasian Collared Dove harbors three haplotypes. There was no mutation in the COI gene, only in the CR. This may be due to the fact that the CR generally had a faster base substitution rate than the COI gene, and this was also the case in this species. In contrast to our results, sequencing of 658 bp of the COI gene from 134 individuals of the Eurasian Collared Dove from around Europe revealed 42 haplotypes (Bagi et al. 2018). It is estimated that European Doves have multiplied to approximately 20-40 million individuals in 50-60 years, and the high genetic diversity of doves in Europe is due to a remarkable population. The Japanese wild Eurasian Collared Dove had a genetic diversity of 0.616, but the California Condor (Gymnogyps californianus), which is feared to become extinct, was 0.543, and the Eastern White Eagle (Aquila adalberti) was 0.322 (Martinez-Cruz et al. 2004; Adams and Villablanca 2007). Compared with these, the values are not considered to be low. As a result of the mismatch distribution analysis, a unimodal was formed with low nucleotide diversity value, and there was no significant difference in SSD. Furthermore, network analysis showed a star shape. These results indicate that the Eurasian Collared Dove has experienced population expansion in the past, but in fact, the current population has been decimated. This pattern of Eurasian Collared Dove may be the immediate result of a series of demographic events over a very short period of time, such as "introduction–population expansion–population decline—bottleneck". All 20 zoo-bred individuals possessed the same haplotype. All the animals currently bred at the zoo excluding zoo E are from the Saitama Prefectural Agriculture and Forestry Research Center, and were bred from four individuals caught in 1966 (Saitama Eurasian Collared Dove Protection Plan). Therefore, if it is inferred that the four individuals were derived from the same maternal line, and there is no particular contradiction with this result. The breeding population of Zoo L breeds wild individuals, and the founder individuals differ from other zoos. In this study, it was found that they had the same haplotype as those raised in other zoos. The major haplotype of the wild population was SD-B, and all zoo-bred individuals retained SD-A. If all zoo-bred individuals were released into the wild, the major haplotype in wild would be SD-A, but even in wild, SD-A is not numerous, so there seems to be no particular problem as genetic pollution. Since only three SD-Cs in the wild population are detected, protection of the haplotype SD-C is an issue that needs to be given the highest priority in order to maintain the genetic diversity of Eurasian Collared Dove. In the future, it will be necessary to maintain the population so as not to further reduce the population of the Eurasian Collared Dove, and to secure a founder holding SD-C and propagate it in a zoo for protection of this dove species. One of the most important factors of the population decrease of the Eurasian Collared Dove may be that the invasion of wild birds into poultry houses has been controlled by avian influenza countermeasures (Saitama Prefecture 2013). Providing such an environment artificially may be necessary for the protection of Eurasian Collared Dove. It should be interpreted with some caution that only maternally derived mtDNA was used in this study. Future microsatellite genotyping may elucidate the genetic diversity of Eurasian Collared Dove in detail.
We sequenced the 778 bp COI gene and the 1140 bp CR in 20 wild Eurasian Collared Doves and 20 zoo-bred in Japan. Comparative analysis revealed three haplotypes from wild individuals in CR, and all zoo-bred individuals had the same haplotype. Also, the haplotypes of the zoo-bred individuals were retained in wild individuals. Phylogenetic analysis revealed that the three haplotypes were genetically related and had the same DNA sequence as Chinese Eurasian Collared Dove individual. In addition, the study confirms that no genetic problems as genetic pollution can occur if a zoo-bred individual is released into the wild for a Japanese Eurasian Collared Dove propagation program.
This study was conducted as part of a survey in Saitama Prefecture. The authors also thank the anonymous reviewers and editor for their expert criticism and valuable suggestions.
KN performed the experiments, analyzed the data, prepared the draft, figures and/or tables, KT, KU, YT, TA and FN collected samples, FN conceived and designed the study, and improved the drafts. All authors read and approved the final manuscript.
Not applicable.
The datasets used and/or analyzed during the current study are available from the corresponding author on reasonable request.
This study followed all applicable institutional guidelines for the care and use of animals and complied with the current laws of the country in which they were performed.
Not applicable.
The authors have no conflicts of interest to report.
|
Chesser RT, Burns KJ, Cicero C, Dunn JL, Kratter AW, Lovette IJ, et al. Check-list of North American birds. American Ornithological Society. 2019. http://checklist.aou.org/taxa.
|
|
Ehnis DA. Fagus mexicana Martínez, su ecología e importancia. Doctoral Thesis. Mexico City: Universidad Autónoma de México; 1981.
|
|
Gual-Díaz M, Rendón-Correa A. Bosques mesófilos de montaña de México diversidad, ecología y manejo. In: Gual-Díaz M, Rendón-Correa A, editors. Bosques mesófilos de montaña de México diversidad, ecología y manejo. 1st ed. Mexico: CONABIO; 2014. p. 27-67.
|
|
Howell SNG, Webb S. A guide to the birds of Mexico and northern central America. England: Oxford University Press; 1995.
|
|
Kardell L. Bokens spridning I Trogds harad. Sartryck Ur Lustgarden. 2005;85: 29-44.
|
|
Magurran AE. Measuring biological diversity. Malden, MA: Blackwell Science Ltd.; 2004.
|
|
Mulligan M. Modelling the tropics-wide extent and distribution of cloud forest and cloud forest loss, with implications for conservation priority. In: Bruijnzeel LA, Scatena FN, Hamilton LS, editors. Tropical montane cloud forests: science for conservation and management. Cambridge: Cambridge University Press; 2010. p. 14-38.
|
|
National Geographic Society. Field guide to the birds of North America. Washington: National Geographic Society; 2006.
|
|
Olvera-Vital A, Rebón-Gallardo MF, Navarro-Sigüenza AG. Bird diversity and taxonomic turnover in the different habitats in Misantla, Veracruz, Mexico: species comparison over time. Rev Mex Biodiv. 2020;91: e913070.
|
|
Pérez-Rodríguez PM. Las hayas de México, monografía de Fagus grandifolia spp. mexicana. 1st ed. Texcoco: Universidad Autónoma de Chapingo; 1999.
|
|
Peterson TR, Edward FC. Aves de México: Guía de Campo, identificación de otras especies encontradas de México, Guatemala, Belice y El Salvador. Mexico City: Editorial Diana; 1989.
|
|
Ralph CJ, Geupel GR, Pyle P, Martin TE, DeSante DF, Milá B. Manual de métodos de campo para el monitoreo de aves terrestres. Albany: Pacific Southwest Research Station, Forest Service, U.S. Department of Agriculture; 1996.
|
|
Rosemier JN, Flaspohler DJ. Island-specific ecological release of small mammals in Lake Michigan and potential consequences for ground-nesting birds: The importance of American Beech (Fagus grandifolia) in structuring small-mammal communities. George Wright Soc. 2006;23: 24-32.
|
|
Roman L, Scatena FN, Bruijnzeel LA. Global and local variations in tropical montane cloud forest soils. In: Bruijnzeel LA, Scatena FN, Hamilton LS, editors. Tropical montane cloud forests: science for conservation and management. Cambridge: Cambridge University Press; 2010. p. 77-89.
|
|
SEMARNAT. SEMARNAT-Secretaría de Medio Ambiente y Recursos Naturales. Diario Oficial. 2010.
|
|
van Perlo B. Birds of Mexico and Central America. Princeton: Princeton University Press; 2006.
|
|
Yui M. Animals of beech forests. In: Murai H, Yamatani K, Kataoka H, Yui M, editors. Natural environment and its conservation on Buna (Fagus crenata) forest. Tokyo: Soft Science Inc.; 1991. p. 193-234 (in Japanese).
|
|
Zaccagnini ME, Thompson JJ, Bernardos JN, Calamari NC, Goijman AP, Canavelli SB. Riqueza, ocupación y roles funcionales potenciales de las aves en relación a los usos de la tierra y la productividad de los agroecosistemas: un ejemplo en la ecoregion pampeana. In: Laterra P, Jobbágy EG, Paruelo JM, editors. Valoración de servicios ecosistémicos: conceptos, herramientas y aplicaciones para el ordenamiento territorial. Chapter: 8. Buenos Aires: Ediciones inta. 2011. p. 185-219.
|
Figures(8) / Tables(2)
| Location | Number | Haplotype ID | |||
| A | B | C | |||
| Wild | Kounosu | 1 | 1 | ||
| Saitama | 1 | 1 | |||
| Satte | 1 | 1 | |||
| Kasukabe | 2 | 1 | 1 | ||
| Misato | 2 | 1 | 1 | ||
| Kuki | 7 | 7 | |||
| Kawashima | 6 | 2 | 3 | 1 | |
| Total | 20 | 6 | 11 | 3 | |
| Zoo | A | 1 | 1 | ||
| B | 2 | 2 | |||
| C | 9 | 9 | |||
| D | 6 | 6 | |||
| E | 2 | 2 | |||
| Total | 20 | 20 | |||
| The number in parenthesis represents the number of samples. Column indicates haplotype ID number | |||||
DownLoad:
CSV
| Specimen | n | Haplotype | Variable site | Haplotype diversity | Nucleotide diversity | Tajima's D | Fu's FS | SSD | rg | τ |
| Wild | 20 | 3 | 2 | 0.616 ± 0.077 | 0.00077 | 0.93886 | 0.69483 | 0.00556 | 0.10557 | 0.961 |
| Zoo | 20 | 1 | 0 | 0 | 0 | – | – | – | – |
DownLoad:
CSV
Email Alerts
RSS Feeds