Thank you for visiting nature.com. You are using a browser version with limited support for CSS. To obtain the best experience, we recommend you use a more up to date browser (or turn off compatibility mode in Internet Explorer). In the meantime, to ensure continued support, we are displaying the site without styles and JavaScript.

# Studbook and molecular analyses for the endangered black-lion-tamarin; an integrative approach for assessing genetic diversity and driving management in captivity

## Abstract

Breeding strategies based on molecular markers have been adopted by ex-situ conservation programs to assess alternative parameters for the genetic diversity estimates. In this work we evaluated molecular and studbook data for captive populations of black-lion-tamarin (BLT), an endangered primate endemic to Brazil’s Atlantic Forest. Pedigree analyses were performed using BLT studbook information collected from 1973 to 2018. We analyzed the whole captive population since its foundation; the current captive population (CCP); and all extant BLTs in the Brazilian captive population (BCP), separately. Microsatellite analyses were implemented on the BCP individuals from the eighth generation (BCP-F8) only to avoid generation overlap. The expected heterozygosity for BCP-F8, using molecular, data was 0.45, and the initial expected heterozygosity was 0.69. Kinship parameters showed high genetic relationships in both pedigree and molecular analyses. The genealogy-based endogamy evidenced a high inbreeding coefficient, while the molecular analyses suggested a non-inbreeding signature. The Mate Suitability Index showed detrimental values for the majority of potential pairs in the CCP. Nevertheless, some individuals evidenced high individual heterozygosity and allele representation, demonstrating good potential to be used as breeders. Thus, we propose the use of molecular data as a complementary parameter to evaluate mating-pairs and to aid management decision-making.

## Introduction

Captive breeding programs have been recognized as a powerful alternative for rescuing endangered species and for biological conservation1,2. Often based on pedigree analyses, ex-situ management plans aim to maintain demographically stable populations, retaining genetic diversity, limiting inbreeding, and avoiding adaptation to captivity1,3,4,5,6. However, this is not an easy task, and consequently captive groups tend to present lower levels of genetic diversity and higher inbreeding rates than expected2,7, challenging the success of these captive breeding programs. On the other hand, wild endangered species often present small and fragmented populations subjected to bottleneck effects and absence of gene flow, and low genetic diversity levels are commonly also observed in nature8,9. This is the case for the black-lion-tamarin (BLT), Leontopithecus chrysopygus (Callitrichidae, Platyrrhini), an endangered primate inhabiting exclusively the Atlantic Forest of São Paulo state in Southeast Brazil8,10.

The population size of L. chrysopygus in nature is small11, currently estimated at a total of a thousand individuals living in a few small forest fragments12. This species was assumed to be extinct about 65 years, when a small population was rediscovered in the Morro do Diabo State Park (SP, Brazil)13. At that time, a population census estimated that only about 200 animals existed in nature. In 1973, the first seven wild individuals of two contiguous subgroups of BLT were brought into captivity, at the Biological Bank of Tijuca in Rio de Janeiro (Rio de Janeiro, Brazil)14. In 1985, because of the construction of the Rosana Hydroelectric dam, invading about 3,000 ha of the protected Morro do Diabo State Park, eight wild groups were rescued. Of these animals, one group of six individuals was brought to the Rio de Janeiro Primatology Center (CPRJ; Guapimirim, RJ, Brazil), and the seven other groups, totaling 31 BLTs, were kept in a vivarium, and transferred to a nearby forest fragment later15,16. However, due to the poor health condition of these transferred animals, only sixteen BLTs (six males, eight females and two animals with no gender information) survived and were relocated to the Zoological Park Foundation of São Paulo State (FPZSP; São Paulo, SP, Brazil), starting a new group in captivity in 198617.

In 1987, the International Committee for the Preservation and Management of BLTs was organized in order to contribute to the management of the captive groups of this species. From this initiative, the studbook for the black-lion-tamarin, describing genealogical records for the captive animals, was created in the same year18. The first captive group of BLT overseas emerged in 1990, when six individuals were transferred from CPRJ to the Jersey Wildlife Preservation Trust (Jersey Zoo, Jersey, Channel Islands), currently known as Durrell Wildlife Conservation Trust (DWCT). The animals kept at Jersey Zoo successfully produced offspring, and some L. chrysopygus were transferred to other institutions in Europe, North America and Australia. However, the majority of these individuals died17, and nowadays there are only extant captive BLT overseas in Jersey8.

Similarly to most ex-situ breeding programs, the management of L. chrysopygus in captivity has been implemented based only on pedigree analyses8, aiming to minimize population average kinship and preserve representative genetic diversity19,20,21. Although this strategy has been considered appropriate to avoid inbreeding22, even if a pedigree has been properly scored for a captive group since its foundation, founder relationships are generally unknown, and for management purposes it is commonly assumed that the founders are unrelated23. Moreover, captive breeding programs often recruit few founders, in general from a single population, representing a small proportion of the total genetic diversity of a species1.

To compensate for the lack of knowledge about the initial genetic diversity and relationships between the founders, various institutions that manage endangered species have recently tried to combine molecular data with pedigree analyses6,24,25,26,27,28, although studies integrating both types of data are still scarce29.

In the present work, we performed studbook and microsatellite analyses to assess population genetic structure and infer demographic and genetic diversity parameters in the captive groups of L. chrysopygus. We analyzed molecular and pedigree data and estimated genetic diversity for F0. The most common pedigree-based index used to choose mates in breeding programs was compared with the individual heterozygosity obtained by microsatellite markers. Our findings suggest that although genealogical analysis has been beneficial, an integrated approach including molecular data might be useful for a better understanding of genetic diversity and the structure of the BLT population in captivity, and for proper metapopulation management.

## Results

### Genealogical and demographic inferences based on pedigree data analyses

The whole captive population of BLTs consists of 517 animals (Supplementary Fig. S1), of which 466 have already died, including 35 wild founders and three individuals with unknown parents (Table 1). The Brazilian captive population of BLTs includes 37 adults recorded in the 2014 studbook30. Of these, 17 individuals were maintained at the Primatology Center of Rio de Janeiro, 16 at the Zoological Park Foundation of São Paulo, and four at the São Carlos Ecological Park (PESC; São Carlos, SP). However, some of these animals were relocated among the zoos during the years 2015–2018, including five BLTs that were recently transferred from both CPRJ (two animals) and FPZSP (three animals) to Jersey Zoo. In addition, other BLTs were born and one wild individual from Patrania municipality was brought to captivity. Currently, there are 55 living animals in the captive population. Eight of them are in Jersey Zoo, one in Magdeburg Zoo (German) and 46 are in Brazil (15 at CPRJ, 26 at the FPZSP, three at PESC, and two at Belo Horizonte Zoological, (BH Zoo; in Minas Gerais state) (Supplementary Table S1).

The pedigree graphical representation for the WCP revealed nine generations of BLTs in captivity up to 2018, with several non-breeding individuals and some others showing higher reproductive rates (Supplementary Fig. S1). Related to the pedigree depth, until the fifth generation back, the completeness level for the WCP was 92% for the parent generation, 71% for the grandparent generation and 45% for the great-grandparent generation. The Brazilian captive population showed an overlap of generations including animals from the 5th, 6th, 7th, and 8th generations. Thus, for the integrative approach, we calculated genetic diversity estimators for the individuals comprising the eighth generation (BCP-F8), which included the descendants from the prior generations without the parents (Fig. 1).

The longest generation interval values were found for father-daughter for the WCP (6.32 years) and father-son for the CCP (11.04 years) populations. The average generation interval for WCP and CCP was 5.44 and 7.57 years, respectively. The generation intervals calculated across all pathways are presented in Table 2. More details of demographic and genealogical results, including age structure, fertility (Mx), mortality (Qx), survival (Lx), expected lambda-λ, instantaneous rate of change of the population (r), and reproductive peaks in captivity are shown in Supplementary Information (Figs. S2S6).

### Measures of the probabilities of gene origin based on pedigree data

The effective number of ancestors (fa) calculated following Boichard et al.31 was 10 for WCP and eight for both CCP and BCP. The effective number of founders (fe) was equal to 10 for WCP, CCP and BCP (Table 3). These results show a markedly lower number of non-captive potentially contributing individuals than the total number of wild animals registered in the current version of the BLT Studbook (Table 1). For CCP, the proportion of remaining genetic diversity (rGD) based on the founder genome equivalent (fge) was 87.2%. When we considered only BCP, rGD was equal to 83.9% (Table 3).

### Inbreeding, mean kinship and effective population size based on pedigree data analyses

The inbreeding coefficient (F) was higher in BCP and CCP than in WCP (Table 4). The inbreeding values ranged from 0.0119 in 1984 to 0.1070 in 2018 (Supplementary Table S2), showing a curve fluctuating according to the number of inbred individuals in each year (Fig. 2).

Mean kinship statistics showed slightly superior values in the CCP and BCP (Table 5). The realized effective population size (NeI) and the value of Nec, which assumes random mating occurring in the near future, are shown in Table 5. The ratio Nec/Ne for CCP was equal to 0.30.

The genetic structure, based on Wright’s F-statistics (FST between groups) and mean coancestry (fij) within and between zoos, is shown in Table 6. The F-statistics evidenced that Jersey Zoo and CPRJ are the most genetically distant captive groups, whereas mean coancestry and FST values showed that PESC and CPRJ are the most related ones.

### Genetic diversity inferences based on molecular and pedigree data integrative analyses

For the integrative approach, we considered the eleven individuals from BCP in the eighth generation (BCP-F8), which were born between 2005 and 2012. Currently, 10 of these are alive and consequently are included in the CCP as well (Fig. 1). The set of 15 microsatellite loci was successfully amplified in these samples, with no indication of null alleles, stuttering, allelic dropout and significant LD (p > 0.05). Despite literature report some issues for dinucleotide loci32,33,34, no genetic inconsistencies were found for these loci, after following the technical procedures employed for DNA amplification and genotyping (see Supplementary Information). The obtained electropherograms (EPGs) evidenced specific allele patterns with proper quality (Supplementary Fig. S8). After sequencing and alignment of the amplicons, the expected motifs were searched, and the microsatellite sequences were confirmed for all heterologous loci.

In total, we computed 31 alleles, ranging from two to three per locus, with an average of 2.06 alleles per locus, and average allelic richness equal to 2.07. The equivalent genetic diversity estimators, based on both pedigree and molecular data, are shown in Table 7. The effective population size (NeI) showed a higher value when calculated through pedigree analyses. The ratio of Ne/N was equal to 0.18 and 0.12 for genealogical and molecular data, respectively. The founder genome equivalent was 1.42, and the mean effective number of alleles was 1.84. The degree of kinship (Mk) based on pedigree data showed a high value concordant with that observed using the pedigree inbreeding index (F = 0.19). Kinship based on molecular data (rm) confirmed a high degree of relatedness. The molecular inbreeding coefficient was negative (f = −0.58), as a consequence of an excess of heterozygosis, the observed mean (Ho = 0.73) being higher than the expected heterozygosity (He = 0.45).

The remaining genetic diversity measured by pedigree analyses was 65%. Remaining genetic diversity and heterozygosity for F0, calculated based on the integrative approach, were 65% and 0.69, respectively. The values of MSI estimated by PMx for all extant BLTs from CCP, including individuals from Jersey, resulted in a total of 480 simulated potential couples, in which 80% were considered at least as slightly detrimental (4, 5, 6, ~) (Fig. 3). In contrast, the individual heterozygosity, based on the IR Index, for the three individuals from FPZP (studbook numbers 471, 472, 497) and the two individuals from CPRJ (studbook number 436, 487), which were recently transferred from Brazil to Jersey, ranged from −0.654 to −0.088 (Table 8), indicating high heterozygosity.

## Discussion

Setting up an efficient captive breeding program requires a precise knowledge of the genetic diversity and genealogical data of the populations to be managed35. In this sense, pedigree analyses can provide relevant information for the management of species in captivity28. However, the effectiveness of pedigree-based approaches depends on its completeness and depth, since deeper pedigrees usually generate more accurate and robust inferences35. According to the present study, 92% of ancestral relationships in the whole captive population of BLTs are well known. Taking into account such high pedigree depth value, the demographic and genetic inferences raised herein, based on the BLT studbook data, should be considered as reliable.

Overall, the captive BLT population is well established; nevertheless, its age structure is typical for a slowly growing population (λ > 1), showing an explicit decline from the year 2001, in both sexes. The whole captive group reached a maximum population size of 114 (59 males and 55 females) in 2000, but in the subsequent years it suffered a drastic and continuous decline, though new births have contributed to the growth of the current captive population in Brazil. We also observed an increase in the average generation interval over the years. These results are quite probably due to management efforts aimed at minimizing inbreeding by the reuse of less related animals as reproducers36, that in this case are the oldest BLTs. In addition, we verified low rates of reproduction of founder and non-founder wild animals, and also a high number of unrelated captive animals that never reproduced at all. Thus, despite the huge efforts to avoid matings between closer relatives, or in recent years to decrease accumulation of inbreeding as much as possible, the BLT captive population has been showing an increase in inbreeding over time and high kinship values.

High rates of inbreeding and kinship can promote genetic diversity loss and inbreeding depression in future generations, compromising fitness-related features such as viability, birth weight and fecundity37. Unfortunately, some possible evidence of inbreeding depression, such as bone deformities, low copulation rates, low sperm motility, high rates of infertility and cleft lip that cause infant deaths during tooth changes, have already been observed in the Brazilian captive population of BLTs (Pissinatti, A., personal communication). Additionally, the European population has experienced a high incidence of gallbladder problems (Wormell, D., personal communication). In spite of this, the short-term goal of the BLT breeding program in captivity has been achieved by the high survival rates in the infant and juvenile age groups. However, the long-term goal for BLT management consists of maintaining genetic diversity levels and avoiding inbreeding depression38.

Captive populations often have a very small number of founders, which are considered unrelated and consequently have inbreeding rates assumed as zero1,23. In our study, we know the origin of the founders, which came from two neighboring groups of the same population that lived in the Morro do Diabo State Park and might be genetically related. Consequently, the kinship and inbreeding values calculated by pedigree analyses were high, compromising the viability38 of the captive population of BLTs in the long-term.

Fortunately, according to measures of probabilities of gene origin, our data showed a greater value of effective size when compared to the effective number of founders, ancestors and founder genome equivalent values. The relationship between the effective size and the population size (NeI/N) shows that the pedigree-based recommendations are being directed to the equalization of the families, and the sex ratio and the number of individuals throughout the generations, aspects considered very advantageous39. Moreover, molecular data have shown a higher observed heterozygosity than expected, which leads us to infer that zoos are managing the population appropriately. Nevertheless, the PMx analyses showed that the MSI values are at least detrimental40 for the majority of potential couples of the CCP. From the total of simulated mate pairs, 174 and 30 showed values of MSI that were slightly detrimental and detrimental, respectively. The remaining ones were considered very detrimental and very highly detrimental. On the other hand, only 20% pairs had MSI values considered as beneficial for breeding programs, whereas the BLTs recently transferred from Brazil to Jersey showed MSI values moderately or slightly beneficial when we simulated pairing with BLTs from Jersey Zoo.

The MSI is the most common parameter used to select mates in captive breeding programs, and considers differences in genetic diversity, kinship, inbreeding coefficient and unknown ancestry, all calculated only by pedigree data40,41,42. Considering the MSI values found here, we estimated the Internal Relatedness index as a complementary parameter to the MSI, in order to gain some insights based on molecular data as well.

The IR index is a method for estimating individual heterozygosity and considers that rare alleles count more than common alleles. Negative IR values indicate higher heterozygosity, whilst positive values are attributed to more homozygous individuals43. In our study, despite the fact that the transferred BLTs have shown moderately or slightly beneficial MSI values, they all showed negative IR values, indicating that these individuals have high heterozygosity, besides allele representativeness, and consequently are valuable as breeders44. In fact, these animals have already mated and successfully produced offspring in Jersey (Wormell, D., personal communication; https://www.durrell.org/wildlife/news/durrell-celebrates-birth-endangered-monkeys/). Alternatively, if only very homozygous individuals are available for forming mate-pairs, genetic differentiation among the potential breeders and their allele representativeness45 must be considered in addition to MSI scores.

Management decisions must take into account the possibility of changes in genetic diversity by mating between genetically more divergent individuals1,45. Previous molecular analysis, using the same set of microsatellites used here, showed private alleles in each captive group from Brazil and Europe, evidencing genetic structuring among them8. In addition, the pedigree analyses performed here pointed to greater genetic differentiation between the Jersey and CPRJ captive groups. It is noteworthy that the animals that successfully mated in Jersey are from CPRJ (487) and FPZSP (472), these latter being descended from the CPRJ group. In this case, the genetic diversity increment was beneficial to the metapopulation management of BLTs46.

Notwithstanding this, changes in the genetic diversity of source and recipient populations, by movement of individuals, are not always beneficial to both populations. Such groups need to be carefully managed to maintain the maximum of allele richness, to avoid inbreeding, but also potential outbreeding depression. Therefore, combining multiple genetic diversity measures, based on both molecular and studbook data, might produce a more robust data set42,47,48,49.

When the initial genetic diversity of the founding captive population is unknown, it is hypothetically considered equal to 1, as proposed by the PMx model commonly used for calculating pedigree parameters5,40. However, our findings suggest that despite the remaining genetic diversity is about 65% in both pedigree and integrated analyses, the expected heterozygosity represented in the founder individuals, based on the integrative approach, would be about 0.69. Such results show a more coherent value of genetic diversity for F0, reinforcing the idea that genetic diversity inferences must be specific for each breeding program and cannot be extrapolated from hypothetical assumptions7,48.

Molecular analyses are essential for populations with unknown genetic diversity and can be relevant to monitoring genetic diversity across generations in conservation actions50,51,52,53. According to recommendations of the ISFG (International Society for Forensic Genetics) for the area of non-human DNA typing34, they have also potential to be used, by the community of forensic scientist, for investigations involving poaching, smuggling and illegal trade of protected species32,54,55

DNA-based studies can still simulate, estimate and compare genetic diversity levels in breeding programs56. Genetic management of threatened species has experienced an increase in the last few years6,29,57,58, and more recently has been improved by a combination of pedigree and molecular information59. For the BLT captive breeding program, we highlight that an integrative approach could be of benefit in terms of allele representativeness and also for considering a more plausible genetic diversity estimate for the founding population.

Overall, to promote the long-term success of the BLT conservation program, we recommend including genetic diversity parameters based on molecular data, in addition to the pedigree analyses and MSI scores. Microsatellite-based values of expected heterozygosity, individual heterozygosity, allele richness, private alleles, population structure, inbreeding and kinship could be monitored over generations, helping to evaluate gains and losses of genetic diversity more effectively, and identifying individuals potentially better suited for reproduction and for relocation in captivity29,42,47. Finally, we must take into account that an integrated in situ and ex situ approach is strongly indicated for the metapopulation management of BLTs and to help shield this species from its imminent risk of extinction, since in nature L. chrysopygus has a small population size and a very low genetic diversity level.

## Methods

### Ethical requirements and research permits

The present study was approved by the Ethics Committee on Animal Experimentation (Federal University of São Carlos, São Carlos, São Paulo, Brazil), under CEUA-UFSCAR number 9805200815; the Authorization System and Biodiversity Information of the Chico Mendes Institute for Biodiversity Conservation (Ministry of Environment, Federal Government, Brazil), under SISBIO-ICMBio numbers 50616-1; and the National System of Genetic Patrimony Management and Associated Traditional Knowledge (Ministry of Environment, Federal Government, Brazil), under SISGEN number A411359. The approved experimental protocols included the capture of live animals in captivity, and the anesthesia using direct inhalation equipment and blood collection procedures. The animals were handled by a veterinarian who released them safely after blood collection. These procedures followed all ethical and legal recommendations proposed by the institutional and licensing committee and the American Society of Primatologists for the Ethical Treatment of Non-Human Primates (https://www.asp.org/society/resolutions/EthicalTreatmentOfNonHumanPrimates.cfm).

### Studbook data and pedigree analyses

We analyzed all records of L. chrysopygus registered in the International Studbook for the black-lion-tamarin (unpublished current version). We considered all BLTs kept in captivity from 1973 to 2018, including the founders, ancestors and their offspring, and we carried out analyses separately for three set of individuals: the whole captive population (WCP), including all living or dead captive BLTs; the current captive population (CCP), comprising all extant captive individuals maintained in Brazil and overseas until 2018; and the Brazilian captive population (BCP), including only living captive BLT adults in Brazil8.

For demographic inferences we implemented three different analyses for evaluating the consequences of the applied random mating system and its evolution over time by using the Endog 4.8 software60. First, we calculated the pedigree depth by considering the proportion of known ancestors per generation for each offspring, and then we added the interval of generations, defined as the mean age of parents when their progeny is selected to be parent, considering the relationships between mother-daughter, mother-son, father-daughter and father-son61. Finally, we estimated the equivalent complete generations based on the proportions of individuals with both known parents. This parameter is also known as the mean equivalent generation (ge) and it is calculated as the sum of all known ancestors $$(\frac{{1}^{n}}{2})$$, where n is the number of the $${i}^{th}$$ generation separating an individual from each known ancestor (e.g. parents = 1, grandparents = 2, great-grandparents = 3, …)62. The complete pedigree was constructed using Pedigree Viewer version 6.5.2.063.

Fertility (Mx) was calculated considering the individual fertility or reproductive potential information for each age class. Mortality (Qx) was estimated as the proportion of individuals entering an age class versus animals that died before reaching the age class x + 1. Survival (Lx) was determined as the proportion of individuals surviving from birth to the beginning of the age group x. The proportional change in population size from one year to the next, based on life table calculations (expected lambda-λ), and the instantaneous rate of change of the population, averaged for males and females (r), were also estimated. A lambda value greater than one indicates an increase in the population. A value of r greater than one also means that the population is increasing. All these estimators were calculated using PMx software40.

For the pedigree-based genetic inferences, we determined genetic diversity by calculating the total effective number of founders (fe)64 and total effective number of ancestors (fa)31, using the Endog 4.8 software60, and founder genome equivalents (fge)64 using PMx40. The degree of remaining genetic diversity (i.e., expected heterozygosity originated by limited numbers of founders and its balanced contribution) was calculated based on the following expression: $$\frac{He}{H0}=1-\left(\frac{1}{2fge}\right)$$, in which H0 = 1. The inbreeding coefficient (F) was estimated to illustrate the trend in mean inbreeding across years. Likewise, mean kinship (Mk) was also calculated as complementary information to that provided by the inbreeding coefficient (F). FST and mean coancestry (fij) were calculated following Caballero and Toro65,66, considering the genetic divergence between each pair of zoos which hold the species based on the pedigree data. These latter parameters were calculated using PMx software40.

The effective population size (Ne) was estimated based on two approaches (NeI and Nec) implemented in Endog version 4.860. First, Ne was calculated to estimate the founder population size and to detect the existence of bottlenecks and possible consequences of the mating strategy, via the individual increase in inbreeding (NeI), as proposed by De la Rosa et al.67. To calculate NeI, the coefficient of individual increases in inbreeding (∆Fi), determined according to Falconer and Mackay68 and modified by Gonzales-Recio et al.69 and Gutiérrez et al.70, was used. The modified method proposed by Gutiérrez et al.70 is considered the most appropriate to analyze permanently subdivided populations. Ne was also calculated using the increase in coancestry (Nec) proposed by Cervantes et al.71, which is suitable when mixing of populations becomes a usual practice. We also calculated the ratio of the effective population size (NeI) to the census size of living captive-born individuals (NeI/N). Mate Suitability Index (MSI) was determined for all potential pairs in the current captive population of BLTs using PMx40.

### Biological samples and molecular analyses

Biological samples of all BLTs from the Brazilian captive population were obtained by collecting about 0.5 mL of fresh blood from each individual, using vacutainers containing EDTA (3.6 mg). The animals were anesthetized by direct induction using inhalation equipment calibrated with isoflurane (2–5%) and oxygen (2 L/min), and were then released back into their respective enclosures. Blood samples were stored at −20 °C for subsequent DNA extraction. Genomic DNA was obtained following the phenol protocol72. The DNA integrity was confirmed using 1% agarose gels under constant voltage (100 V for 45 min) (Supplementary Fig. S7A) and the quantification was performed using GE NanoVue Plus, GE Healdthcare Spectophotometer.

Polymerase chain reactions (PCRs) for the microsatellite amplifications followed procedures proposed by Ayala-Burbano et al.8. We firstly tested a panel of 22 loci previously described for Leontopithecus species73,74,75 (Supplementary Table S3), and posteriorly selected 15 polymorphic loci. PCR-amplified products were visualized in 2% agarose gel (Supplementary Fig. S7B). Genotyping were performed in an ABI3730XL automatic sequencer (Applied Biosystems, Foster City, CA, USA), using GS 500 Liz size standard, and the alleles were scored in the software Geneious version 6.0.6 (https://www.geneious.com). Each sample genotyped as homozygous was confirmed by a minimum of three replications. We also performed multiple PCRs for random samples, in order to identify genetic inconsistencies, according to recommendations proposed by the ISFG (International Society for Forensic Genetics) for the area of non-human DNA typing34. More details related to the technical procedures employed for DNA amplification and genotyping of the STR (Short Tandem Repeats) loci are available in Supplementary Information.

Before the statistical analyses, we estimated the occurrence of null alleles, allelic dropout and stuttering for all scored alleles using Micro-Checker76. Subsequently, lack of linkage disequilibrium (LD) between loci was verified in Genepop version 4.0.1077. We used the linkage disequilibrium method to assess the effective population size. Genetic diversity parameters were inferred by calculating the number of alleles (Na), effective number of alleles (Nae), expected (He) and observed (Ho) heterozygosity using GenAlEx version 6.478.

The proportion of remaining genetic diversity represented in the eighth generation of the BCP was calculated as $$\frac{{\rm{He}}}{{\rm{H}}0}={\left(1,-,\frac{1}{2{\rm{Ne}}}\right)}^{{\rm{t}}}$$, in which H0 is the initial heterozygosity in the F0 generation, He is the expected heterozygosity calculated by molecular data, t is the number of generations, and Ne is the number of individuals that produced offspring in a specific generation. Ne was calculated by harmonic mean79, where $${\rm{Ne}}=\frac{1}{\frac{1}{{\rm{Ne}}1}+\frac{1}{{\rm{Ne}}2}+\frac{1}{{\rm{Ne}}3}\ldots \frac{{\rm{N}}}{{\rm{Net}}-1}}$$. From the ratio between molecular heterozygosity expected for F8 (He) and for F0 (H0), we calculated the remaining genetic diversity (rGD), considering the effective population size, and then we estimated the genetic diversity for F0.

Allelic richness (Ra) and inbreeding coefficient (f) were calculated using Fstat version 2.9.3.280. The mean relatedness (rm) between individuals was estimated using Coancestry81. This software calculates seven different relatedness estimators, and after testing all of them, we choose the estimator based on Triade likelihood (TrioML), which showed the smallest variance among all the estimators tested81.

Individual heterozygosity, based on the internal relatedness index (IR)82 was calculated for the individuals recently transferred from Brazil to England, using GENHET83, in order to add a relevant molecular genetic diversity parameter to the MSI obtained from pedigree data.

## References

1. Rudnick, J. A. & Lacy, R. C. The impact of assumptions about founder relationships on the effectiveness of captive breeding strategies. Conserv. Genet. 9, 1439–1450 (2008).

2. Frankham, R. Challenges and opportunities of genetic approaches to biological conservation. Biol. Conserv. 143, 1919–1927 (2010).

3. Foose, T. & Ballou, J. Management of small populations. International Zoo Yearbook 26–41, https://doi.org/10.1111/j.1748-1090.1988.tb03194.x (1988).

4. Hedrick, P. & Miller, P. Conservation genetics: theory and management of captive populations. In Conservation of biodiversity for sustainable development. (ed. Sandlund OT, Hindar K, B. A.) (1992).

5. Lacy, R. Clarification of Genetic Terms and Their Use in the Management of Captive Populations. vol. 14 (1995).

6. Ivy, J. A., Miller, A., Lacy, R. C. & DeWoody, J. A. Methods and prospects for using molecular data in captive breeding programs: an empirical example using Parma wallabies (Macropus parma). J. Hered. 100, 441–454 (2009).

7. Ivy, J. A. & Lacy, R. C. A comparison of strategies for selecting breeding pairs to maximize genetic diversity retention in managed populations. J. Hered. 103, 186–196 (2012).

8. Ayala-Burbano, P. A. et al. Genetic assessment for the endangered black lion tamarin Leontopithecus chrysopygus (Mikan, 1823), Callitrichidae, Primates. Am. J. Primatol. 79, e22719 (2017).

9. Frankham, R. Genetic adaptation to captivity in species conservation programs. Mol. Ecol. 17, 325–33 (2008).

10. Kierulff, M. C. M., Rylands, A. B., Mendes. S.L. & de Oliveira, M. M. Leontopithecus chrysopygus.The IUCN Red List of Threatened Species 2008., https://doi.org/10.2305/IUCN.UK.2008.RLTS.T11505A3290864.en (2008).

11. Ballou, J. D. & Valladares-Pádua, C. B. Metapopulation Action Plan. (1997).

12. Rezende, G. Mico-leão-preto: a História de Sucesso na Conservação de uma Espécie Ameaçada. (Matrix Editora, 2014).

13. Coimbra-Filho, A. F. Acerca da redescoberta de Leontopithecus chrysopygus (Mikan, 1823) e apontamentos sobre sua ecologia. Rev. Bras. Biol. 30, 609–615 (1970).

14. Coimbra-Filho, A. F. Os Sagüis do Gênero Leontopithecus Lesson, 1840- Callithricidae- Primates-. (Universidae Federal do Rio de Janeiro, 1976).

15. Valladares-Pádua, C. B. & Rylands, A. Lion tamarins rescued. Oryx 20, 71–72 (1986).

16. Carvalho, C. T. & Carvalho, C. F. A organização social dos sauís-pretos, na reserva em Teodoro Sampaio, São Paulo (Primates Callithricidae. Rev. Bras. Zool. 6(707), 717 (1989).

17. Kleiman, D. G. & Rylands, A. B. Lion tamarins: Biology and conservation. (Smithsonian, 2002).

18. Simon, F. Comitê Internacional de Preservação e Manejo do Mico-leão-Preto, Fundação Parque Zoológico de São Paulo, São Paulo. in Micos leões: biologia e conservação. (ed. Kleiman, D. G.; Rylands, A. B. (Orgs.) (1988).

19. Fernández, B. J. & Toro, M. A. The use of mathematical programming to control inbreeding in selection schemes. J. Anim. Breed. Genet. 116, 447–466 (1999).

20. Lacy, R., Ballou, J. D., Princee, F., Starfield, A. & Thompson, E. Pedigree analysis for population management. in Population Management for Survival and Recovery (eds. Ballou, J. D., Gilpen, M. & Foose, T.) 57–75 (New York: Columbia University Press., 1995).

21. Sonesson, A. K. & Meuwissen, T. H. E. Minimization of rate of inbreeding for small populations with overlapping generations. Genet. Res. (Camb). 77, 285–292 (2001).

22. Marshall, T. C., Sunucks, P., Spalton, J. A. & Pemberton, J. M. Use of genetic data for conservation management: the case of the Arabian oryx. Anim. Conserv. 2, 269–278 (1999).

23. Ballou, J. Calculating inbreeding coefficients from pedigrees. In Genetics and conservation: a reference for managing wild animal and plant populations (ed. Schonewald-Cox, C. M., Chambers, S. M., MacBryde B, T. W.) (The Benjamin/Cummings Publishing Company Inc., Menlo Park, 1983).

24. Gautschi, B., Müller, J. P., Schmid, B. & Shykoff, J. A. Effective number of breeders and maintenance of genetic diversity in the captive bearded vulture population. Heredity (Edinb). 91, 9–16 (2003).

25. Ogden, R., Langenhorst, T., McEwing, R. & Woodfine, T. Genetic markers and sample types for pedigree reconstruction in Grevy’s zebra (Equus grevyi). Der Zool. Garten 77, 29–35 (2007).

26. McGreevy, T. J., Dabek, L. & Husband, T. P. Genetic evaluation of the Association of Zoos and Aquariums Matschie’s tree Kangaroo (Dendrolagus matschiei) captive breeding program. Zoo Biol. 30, 636–646 (2011).

27. Henkel, J. R. et al. Integrating microsatellite and pedigree analyses to facilitate the captive management of the endangered Mississippi sandhill crane (Grus canadensis pulla). Zoo Biol 31, 322–335 (2012).

28. Ferrie, G. M. et al. Identifying parentage using molecular markers: Improving accuracy of studbook records for a captive flock of marabou storks (Leptoptilus crumeniferus). Zoo Biol. 32, 556–564 (2013).

29. Ito, H., Ogden, R., Langenhorst, T. & Inoue-Murayama, M. Contrasting results from molecular and pedigree-based population diversity measures in captive zebra highlight challenges facing genetic management of zoo populations. Zoo Biol. 36, 87–94 (2017).

30. Wormell, D. International Studbook for the Black Lion Tamarin Leontopithecus chrysopygus. (Durrell Wildlife Conservation Trust, 2014).

31. Boichard, D. The value of using probabilities of gene origin to measure genetic variability in a population. Genet Sel Evol 29, 5–23 (1997).

32. Iyengar, A. Forensic DNA analysis for animal protection and biodiversity conservation: A review. J. Nat. Conserv. 22, 195–205 (2014).

33. Andreassen, R. et al. A forensic DNA profiling system for Northern European brown bears (Ursus arctos). Forensic Sci. Int. Genet. 6, 798–809 (2012).

34. Linacre, A. et al. ISFG: Recommendations regarding the use of non-human (animal) DNA in forensic genetic investigations. Forensic Sci. Int. 5, 501–505 (2011).

35. Goyache, F. et al. Using pedigree information to monitor genetic variability of endangered populations: the Xalda sheep breed of Asturias as an example. J. Anim. Breed. Genet. 120, 95–105 (2003).

36. Nagy, I. et al. Genetic diversity and population structure of the synthetic pannon white rabbit revealed by pedigree analyses. J. Anim. Sci. 88, 1267–1275 (2010).

37. Templeton, A. R. & Read, B. Factors eliminating inbreeding depression in a captive herd of speke’s gazelle (Gazella spekei). Zoo Biol. 199, 177–199 (1984).

38. Escarlate-Tavares, F., Mafra, M. & Jerusalinsky, L. Plano de ação nacional para a Conservação dos mamíferos da Mata Atlântica Central. (2016).

39. Frankham, R., Briscoe, D. A. & Ballou, J. D. Introduction to conservation genetics. (Cambridge University Press, 2002).

40. Lacy, R., Ballou, J. & Pollak, J. PMx: software package for demographic and genetic analysis and management of pedigreed populations. Methods Ecol. Evol. 3, 433–437 (2012).

41. Ballou, J. D., Earnhardt, J. & Thompson, S. MateRx: Genetic Management Software. (2001).

42. Ralls, K. & Ballou, J. D. Genetic status and management of California condors. Condor 106, 215 (2004).

43. Amos, W. et al. The influence of parental relatedness on reproductive success. Proc. R. Soc. B Biol. Sci. 268, 2021–2027 (2001).

44. Aparicio, J. M., Ortego, J. & Cordero, P. J. What should we weigh to estimate heterozygosity, alleles or loci? Mol. Ecol. 15, 4659–4665 (2006).

45. Ralls, K. et al. Call for a paradigm shift in the genetic management of fragmented populations. Conserv. Lett. 11, 1–6 (2018).

46. Valladares-Pádua, C. B., Ballou, J. D., Saddy, M. C. & Cullen, L. Metapopulation Management for the Conservation of Black Lion Tamarins. in Lion Tamarins Biology and Conservation (eds. Kleiman, D. & Rylands, A.) (Smithsonian Press, 2001).

47. López-Cortegano, E., Pérez-Figueroa, A. & Caballero, A. Metapop 2: Re - implementation of software for the analysis and management of subdivided populations using gene and allelic diversity. Mol. Ecol. Resour. 19, 1095–1100 (2019).

48. Jost, L., Archer, F., Flanagan, S., Hoban, S. & Latch, E. Differentiation measures for conservation genetics. Evol. Appl. 1139–1148, https://doi.org/10.1111/eva.12590 (2017).

49. Zhang, M. et al. Global genomic diversity and conservation priorities for domestic animals are associated with the economies of their regions of origin. Nature 1–12, https://doi.org/10.1038/s41598-018-30061-0 (2018).

50. Russello, M. A. & Amato, G. Ex situ population management in the absence of pedigree information. Mol. Ecol. 13, 2829–2840 (2004).

51. Fienieg, E. & Galbusera, P. The use and integration of molecular DNA information in conservaion breeding programmes: a review. J. Zoo Aquarium Res. 1(2), 44–51 (2013).

52. Jones, K. L. K. et al. Refining the whooping crane studbook by incorporating microsatellite DNA and leg-banding analyses. Conserv. Biol. 16, 789–799 (2002).

53. Marsden, C. D., Verberkmoes, H., Thomas, R., Wayne, R. K. & Mable, B. K. Pedigrees, MHC and microsatellites: an integrated approach for genetic management of captive African wild dogs (Lycaon pictus). Conserv. Genet. 14, 171–183 (2013).

54. Estrada, A., Raboy, B. E. & Oliveira, L. C. Agroecosystems and primate conservation in the tropics: a review. Am. J. Primatol. 74, 696–711 (2012).

55. Oklander, L. I., Caputo, M., Solari, A. & Corach, D. Genetic assignment of illegally trafficked neotropical primates and implications for reintroduction programs. Cornell Univ. (2019).

56. Wang, Z., Bovik, A. C., Sheikh, H. R. & Simoncelli, E. P. Image quality assessment: from error visibility to structural similarity. IEEE Trans. image Process. 13, 600–612 (2004).

57. Carroll, S. P. et al. Applying evolutionary biology to address global challenges. Science (80-.). 346, 1–16 (2014).

58. Smith, T. B. et al. Prescriptive evolution to conserve and manage biodiversity. Anu. Rev. Ecol. Evol. Syst. 45(1), 1–1.22 (2014).

59. Grueber, C. E., Waters, J. M. & Jamieson, I. G. The imprecision of heterozygosity-fitness correlations hinders the detection of inbreeding and inbreeding depression in a threatened species. Mol. Ecol. 20, 67–79 (2011).

60. Gutierrez, J. P. & Goyache, F. A note on ENDOG: a computer program for analysing pedigree information. 122, 172–176 (2004).

61. James, J. W. A note on selection differential and generation length when generations overlap. Anim. Prod. 24, 109–112 (1977).

62. Maignel, L., Boichard, D. & Verrier, E. Genetic variability of french dairy breeds estimated from pedigree infonnation. Interbull Bull 14, 49–54 (1996).

63. Kinghorn, B. P. Pedigree Viewer-a graphical utility for browsing pedigreed data sets. In 5th World Congress on Genetics Applied to Livestock Production vol. 22 85–86 (1994).

64. Lacy, R. Analysis of founder representation in pedigrees - founder equivalents and founder genome equivalents. Zoo Biol. 8, 111–123 (1989).

65. Caballero, A. & Toro, M. Interrelations between effective population size and other pedigree tools for the management of conserved populations. Genet. Res. (Camb). (2000).

66. Caballero, A. & Toro, M. A. Analysis of genetic diversity for the management of conserved subdivided populations. Conserv. Genet. 3, 289–299 (2002).

67. De la Rosa, A. J. M., Cervantes, I. & Gutiérrez, J. P. Equivalent effective population size mating as a useful tool in the genetic management of the Ibicenco rabbit breed (Conill Pages d’ Eivissa). Czech J. Anim. Sci. 2016, 108–116 (2016).

68. Falconer, D. S. D. & Mackay, T. T. F. C. Introduction to quantitative genetics. (Longman Group Limited, 1996).

69. González-Recio, O., López de Maturana, E. & Gutiérrez, J. P. Inbreeding depression on female fertility and calving ease in spanish dairy cattle. J. Dairy Sci. 90, 5744–5752 (2007).

70. Gutiérrez, J., Cervantes, P. & Goyache, I. F. Improving the estimation of realized effective population sizes in farm animals. J.Anim.Breed.Genet. 126, 327–332 (2009).

71. Cervantes, I., Goyache, F., Molina, A., Valera, M. & Gutie, J. P. Estimation of effective population size from the rate of coancestry in pedigreed populations. J. Anim. Breed. Genet. 128, 56–63 (2011).

72. Sambrook, J., Fritsch, E. F. & Maniatis, T. Molecular cloning: A laboratory manual Cold Spring Harbor. (1989).

73. Perez-Sweeney, B. M. et al. Dinucleotide microsatellite primers designed for a critically endangered primate, the black lion tamarin (Leontopithecus chrysopygus). Mol. Ecol. 5, 198–201 (2005).

74. Galbusera, P. H. A. & Gillemot, S. Polymorphic microsatellite markers for the endangered golden-headed lion tamarin, Leontopithecus chrysomelas (Callitrichidae). Conserv. Genet. 9, 731–733 (2008).

75. Grativol, A., Ballou, J. & Fleischer, R. Microsatellite variation within and among recently fragmented populations of the golden lion tamarin (Leontopithecus rosalia). Conserv. Genet. 2, 1–9 (2001).

76. Van Oosterhout, C., Hutchinson, W. F., Wills, D. P. M. & Shipley, P. MICRO-CHECKER: software for identifying and correcting genotyping errors in microsatellite data. Molecular Ecology Notes 4, 535–538 (2004).

77. Rousset, F. GENEPOP’007: A complete re-implementation of the GENEPOP software for Windows and Linux. Mol. Ecol. Resour. 8, 103–106 (2008).

78. Peakall, R. O. D. & Smouse, P. E. GENALEX 6: genetic analysis in Excel. Population genetic software for teaching and research. Mol. Ecol. Notes 6, 288–295 (2006).

79. Frankham, R., Ballou, J.D. & Briscoe, D. A. Inroduction to Conservation Genetics. (2010).

80. Goudet, J. FSTAT, A program to estimate and test gene diversities and fixation indices. 486–486 (2001).

81. Wang, J. Coancestry: a program for simulating, estimating and analysing relatedness and inbreeding coefficients. Mol. Ecol. Resour. 11, 141–145 (2011).

82. Amos, W. & Balmford, A. When does conservation genetics matter? Heredity (Edinb). 87(3), 257–265 (2001).

83. Coulon, A. Genhet: an easy-to-use R function to estimate individual heterozygosity. Mol. Ecol. Resour. 10, 167–9 (2010).

## Acknowledgements

The authors are thankful to Zoological Park Foundation of São Paulo State, Primatology Center of Rio de Janeiro, Ecological Park of São Carlos, Durrell Wildlife Conservation Trust (Jersey Zoo) for supporting sample collections; to ICMBio (Chico Mendes Institute for Biodiversity Conservation, Ministry of Environment, Brazil) for providing the permits (SISBIO); and to Coordenação de Aperfeiçoamento de Pessoal de Nível Superior (CAPES, Finance Code 001), Fundação de Apoio à Pesquisa do Estado de São Paulo (FAPESP, 2020/03986-8), and Conselho Nacional de Desenvolvimento Científico e Tecnológico (CNPq, 304477/2018-4) for the research financial support. We also thanks Eluned Catrin Price for the editing suggestion.

## Author information

Authors

### Contributions

P.A.A.B. and P.D.F. designed and executed the study; M.C.M., D.W. and A.P. provided the biological samples and studbook information; P.M.G.Jr. supported the analyzes for the remaining genetic diversity estimates; P.A.A.B. performed the statistical analyzes and generated the figures and tables; P.A.A.B. and P.D.F. wrote the manuscript; and all co-authors mentioned here participated in the discussion and editing of the article.

### Corresponding authors

Correspondence to Paola Andrea Ayala-Burbano or Patrícia Domingues de Freitas.

## Ethics declarations

### Competing interests

The authors declare no competing interests.

Publisher’s note Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.

## Rights and permissions

Reprints and Permissions

Ayala-Burbano, P.A., Galetti Junior, P.M., Wormell, D. et al. Studbook and molecular analyses for the endangered black-lion-tamarin; an integrative approach for assessing genetic diversity and driving management in captivity. Sci Rep 10, 6781 (2020). https://doi.org/10.1038/s41598-020-63542-2

• Accepted:

• Published:

• DOI: https://doi.org/10.1038/s41598-020-63542-2

• ### Genetic management on the brink of extinction: sequencing microsatellites does not improve estimates of inbreeding in wild and captive Vancouver Island marmots (Marmota vancouverensis)

• Kimberley G. Barrett
• Geneviève Amaral
• Jamieson C. Gorrell

Conservation Genetics (2022)

• ### White-naped mangabeys’ viable insurance population within European Zoo Network

• Carlos Iglesias Pastrana
• Francisco Javier Navas González
• María Teresa Abelló

Scientific Reports (2021)