The inexact type locality and characters in the original description suggest that Copris curvifrons represents a junior synonym of X. dentilabris rather than X. dewitzi (Davis et al. 2020).

This species is listed as Vulnerable on the basis that this species has an extent of occurrence of approximately 10,500 km², it has been recorded from only four localities (and remaining forest patches are highly fragmentary either naturally or by transformation), and a continuing decline in the extent and quality of its habitat is inferred from widespread pressures on remaining Southern Mistbelt Forest, particularly from forestry.

This species is endemic to the eastern escarpment of KwaZulu Natal, Republic of South Africa (Davis et al. 2020). A report from Zimbabwe is "undoubtedly" an error (Davis et al. 2020). Its area of occupancy is not reliably quantifiable, but is likely to be very small due to its apparent association with a very restricted, highly fragmentary, naturally patchy forest type suggests that it is likely to be very small (A. Davis pers. comm. 2023). It has been recorded from only four localities but could be more widespread, although remaining forest patches are highly fragmentary either naturally or by transformation. It has been recorded between 999 and 1,645 m asl (Davis et al. 2020).

Except for 4-5 specimens obtained from the largest forest patch around 2005-2006, it appears to be known only from museum material (A. Davis pers. comm. 2023). There has been no effort to search for it. If it relies on closed-canopy forest it may have declined in proportion to the rate of canopy loss within its range, which has amounted to 24% in the 10 years to 2021 based on data from Global Forest Watch.

There are no quantitative data on this species' habitat preferences: three of the four known localities are inexact but presumably from forest patches within a grassland matrix. The one precise locality (iNhlosane Mountain) lies within Southern Mistbelt Forest (Davis et al. 2020). This is the largest remaining forest patch on iNhlosane Mountain, which has an area of 2.4 km² (A. Davis pers. comm. 2023). The species is "undoubtedly" a forest specialist confined to extremely small, isolated patches of Southern Mistbelt Forest, and it is replaced in the surrounding grassland by a related species, Xinidium dentilabris (A. Davis pers. comm. 2023). This habitat is closed canopy forest (defined as 30% or greater canopy cover) (A. Davis pers. comm. 2023). Three records are from sites mapped to natural grassland, but were presumably instead taken from forest and every site is close to forest - A. Davis pers. comm. 2023). A Dung Beetle Research Unit record reportedly taken from sandy loam in pasture is likely based on inferred habitat from a grid reference rather than specimen data (Davis et al. 2020). The only available food record is from cattle dung (Davis et al. 2020). It is probably flight-active at night between January and March (Davis et al. 2020).

This species is thought likely to be reliant on patches of upland forest. This is however an inference from a single precise locality and the presumed locations of three inexact sites, and so is in need of confirmation (Davis et al. 2020). The precise locality is on a mountain surrounded by tree monocultures and transformed grasslands (A. Davis pers. comm. 2023). All three imprecise localities map to grassland with nearby small forest patches next to roads, of which none is greater than 1.7 km² in area. It is presumed that the specimens were collected from these forest patches (A. Davis pers. comm. 2023). These patches are variously close to or have been mostly replaced by plantations, or are partly degraded (A. Davis pers. comm. 2023). It is unknown whether any of these patches has formal protection, and if not they are likely to be highly sensitive to impacts from tourist traffic or forestry (A. Davis pers. comm. 2023). Mismanagement of fires in surrounding grassland, uncontrolled harvesting of timber and firewood, and overexploitation of non-timber resources are regarded as general threats to Southern Mistbelt Forest by von Maltitz et al. (2003). Observations include a record from reportedly from pasture and Davis et al. (2020) state that 'available observational data is in conflict', however this is thought to be an error of resolution and that record was presumably taken in forest (A. Davis pers. comm. 2023). Forest decline was ongoing as of at least 2021, based on data from Global Forest Watch.

There is no known use of or trade in this species.

It is unclear whether this species occurs within official conservation areas, but the exact locality coincides with a 40 ha patch of native forest on iNhlosane Mt. (Davis et al. 2020) which may lie within the Dargle Nature Conservancy (A. Davis pers. comm. 2023). Further research is needed to clarify its extent of occurrence, area of occupancy and its ecological requirements (Davis et al. 2020), including a transect survey between forest and adjacent grassland to confirm its expected association with forest.