The black or Myanmar snub-nosed monkey (Rhinopithecus strykeri) was discovered in the Gaoligong Mountains of northeastern Kachin state, Myanmar in 2010, and was subsequently found in the mountains of northwestern Yunnan, China in 2011. Across these regions, there were an estimated 14-15 sub-populations with approximately 950 individuals in total (10 sub-populations with 490-620 individuals in China, and 4-5 sub-populations with 260-330 individuals in Myanmar). However, teams of people conducting field surveys and camera trap studies, of which I was part, only confirmed five sub-populations with 400 individuals on the Sino-Myanmar border from data collected 2012-2017. Based on approximately two years field searching, I and my colleagues discovered one sub-population (Luoma population) in the Gaoligong Mountains and conducted another 203 days of field observation to collect dietary data. I also conducted cafeteria feeding trials with 600 wild plant species on two captive individuals housed at Yaojiaping Wildlife Rescue Centre in the Gaoligong Mountains National Nature Reserve. I found that R. strykeri can potentially consume 593 items from more than 170 food plants of trees, bushes, and herbs representing 76 genera and 41 plant families, as well as 15 species of lichen. Among these food items and species, 14 plant species and four lichen species also are consumed by the wild monkeys as well. The food plants mainly distribute in intact sub-tropical evergreen broadleaf forests and hemlock-broadleaf mixed forests at an altitude of 2200-3000 m. Based on interview surveys, camera trap records, and habitat distribution modelling, I confirm this is the main elevational range used by R. strykeri. Nutritional studies and comparisons of 100 leaf items the monkeys selectively consumed (n = 70 plant species) with the nutrient content of 54 leaf items (n = 48 plant species) the monkeys’ avoided in spring and autumn reveal that R. strykeri preferentially select leaves high in moisture (77.7%), crude protein (21.2%), total nonstructural carbohydrates (34.9%) and phosphorus (0.37%) while tending to avoid foods with a neutral detergent fibre content close to 35%. Foods selected in autumn were characterized by a higher amount of metabolisable energy than those rejected (1350 kJ/100g vs. 1268 kJ/100g). Random Forests modeling, an ensemble learning method, indicated that foods consumed during the two seasons were selected primarily based on their proportion of moisture, crude protein, neutral detergent fibre, metabolisable energy, phosphorus and total nonstructural carbohydrates. This nutritional profile is similar to other snub-nosed monkeys. Using interview-based survey data and MAXENT modelling of R. strykeri along the Sino-Myanmar border, I found that R. strykeri may inhabit a range from E98°20′–98°50′ to N25°40′–26°50′. Within this range, high-quality habitat at 1420 km2, medium-quality habitat at 750 km2, and low-quality habitats at 1410 km2. Only 13.9% of the highly suitable habitat (medium + core habitat) for R. strykeri falls within protected areas in China. Approximately 2.6% of the entire habitat has been lost in the past 15 years, 96% of which has been in Myanmar. Two national parks (Imawbum National Park in Myanmar and Nujiang Grand Canyon National Park in China) are therefore proposed for saving this species. Lastly, for structuring a systematic transboundary conservation network in the highly-biodiverse but poorly-studied Gaoligong Mountains region, I used interview-based survey results (on animal distribution data) of three taxa (Primates, Pheasants and Mishmi Takin) and identified five flagship species (R. strykeri, Hoolock tianxing, Trachypithecus shortridgei, Lophophorus sclateri, Budorcas taxicolor) as surrogates of community biodiversity in the Gaoligong Mountains. After confirming the reliability of species distribution data via selective field surveys, I applied multicriteria decision analysis techniques along with data on habitat suitability (MAXENT Models) to highlight areas for transboundary conservation efforts. My results indicate that approximately 83.4% (10,398.7 km2) of remaining habitat with high conservation value for each of the five flagship species is unprotected. This includes six large zones separated by rivers and human settlements that should be designated as transboundary World Nature Heritage, National Parks, or Wildlife sanctuaries along the northern Sino-Myanmar border. Accordingly, I propose related conservation actions and policies for transboundary conservation in the Gaoligong Mountains along the northern Sino-Myanmar border.