The application of the names Eryx tataricus and E. miliaris to different regional populations has historically been complex, and multiple authors have found that at least some samples of E. tataricus fall within the range of variation for E. miliaris (e.g. Ezkandarzadeh et al. 2013, Reynolds et al. 2014). The two taxa were formally synonymised by Eskandarzadeh et al. (2020), largely based on a sampling of Iranian populations. Research elsewhere (e.g. China - B. Cai pers. comm. 2022) supports this arrangement, and this assessment follows Eskandarzadeh et al. (2020) and Uetz et al. (2022) in treating E. tataricus as a junior synonym of E. miliaris.

This concept includes the former subspecies Eryx tataricus speciosus (synonymised within a monotypic E. tataricus by Reynolds and Henderson 2018) but excludes the E. t. vittatus. The latter is recognised as the full species E. vittatus by several recent authors and accepted by Reynolds and Henderson (2018), although there remains little consensus on the appropriate status of this taxon and Reynolds and Henderson (2018) note that differences are "slight" at the molecular level.

European regional assessment: Least Concern (LC)
EU 27 regional assessment: Not Recorded

The Dwarf Sand Boa is assessed as Least Concern for Europe in view of its wide distribution, presumed large population, it occurs in a number of protected areas, and although there is evidence of decline and range contraction in at least part of European Russia it is unlikely to be declining fast enough to qualify for listing in a more threatened category. The species does not occur within the EU 27.

In the European region, this species occurs only in European Russia, reaching its western range limit in the southeastern portion of European Russia. It occurs east of the Volga and sporadically in the south of the Astrakhan region and the east of Kalmykia, as well as in the Stavropol region (Mazanaeva and Orlov 2021).

Outside the European region, Russian subpopulations occur in the northeast of Chechnya in Zaterechye (Tersky sandy massif) and in Dagestan in the southern part of the Nogai region (Mazanaeva and Orlov 2021). Unpublished reports exist from the north of the Tarumovsky region (Mazanaeva and Orlov 2021).

Globally, the ranges outside Europe from the Caspian Sea in the east through northern and central Iran, Afghanistan, Kazakhstan, the sandy deserts of Middle Asia (Turkmenistan and Uzbekistan) to China (where it ranges from Xinjiang through Gansu to western Nei Mongol and Ningxia) and Mongolia (Zhao and Adler 1993, Bannikov et al. 1977, Ananjeva et al. 1997, 1998, 2006, Terbish et al. 2013). It probably occurs much more widely than presently known in the Kyzylkum (Uzbekistan), where suitable habitat is extensive (Showler 2018). In Pakistan, it has been recorded from northwestern Balochistan (Minton 1966). It ranges from sea level (and as low as 100 m below sea level in the Turpan basin; L. Shi pers. comm. 2022) to around 2,200 m asl (Kamiali 2020)

This is generally a common species, however, some subpopulations are declining. The subpopulations previously assigned to the (now invalid) subspecies Eryx miliaris nogaiorum, the form recognised from most of the European range, occurs at low densities in east Ciscaucasia, from 0.001 to one individual per hectare (mean 0.1 /ha). On the left bank of the Volga-Akhtuba floodplain, the population density was 0.3 ind./ha, and 0.03 ind./ha on the right bank (Mazanaeva and Orlov 2021). This is suggestive of a significant decline since the early 20^th Century when seven animals were encountered in a single day on Bazhiganskie sands (Doronin 2013). Although this study area was outside the European Red List region, the overall population is suspected to be declining throughout Russia (Mazanaeva and Orlov 2021). Conversely, in the Astrakhan region, the population is estimated to be relatively stable. In Kalmykia studies of local subpopulations recorded densities along transects ranging from 6–14 ind./km to as little as 2–3 ind./ha (the latter in the extreme north) (Mazanaeva and Orlov 2021).

This species is widely distributed in sandy deserts, in shifting sand dunes, and semi-stabilized sand dunes. It prefers relatively loose soils on different types in deserts and semi-deserts (sagebrush Artemisia-glasswort Salsola desert and glasswort desert), and avoids sandy massifs devoid of vegetation. Sometimes, animals can be found in clay and loess deserts, on the takyr with patches of vegetation near the sands, on the slopes of the ravines and on the margins of irrigated lands, as well as in the dry foothills on the valleys with sandy-clayish soil. In Russia, it is less common in clayey sagebrush-ephemeral semi-desert than in areas of mobile or semi-fixed sands and is most common along the edges of dune sands and in the burrows of rodent colonies (Darewskij 1993, Mazanaeva and Orlov 2021). It may also be encountered in vineyards. Animals often hide within the sand and use burrows of rodents and ruins as refuges.

It is nocturnal during the hot part of the year, and is common on the surface in spring. The period of activity lasts from March to October over most of its range; and in the area of eastern Ciscaucasia and Kazakhstan from April to September. In July and September, it gives birth to 4-21 live young, with an average litter size of 15. It has a maximum life expectancy 25 years (Darewskij 1993, Mazanaeva and Orlov 2021).

In Kalmykia, the main reason for the decline in abundance is the reduction in the area of open sands due to grazing pressure (over 30 cattle per 1 ha of land). The same pressure is resulting in the spread of large-hilly, weakly fixed sandy deserts in the Astrakhan region, which reduces habitat quality for this species, although evidence for consistent decline in the Astrakhan region is currently lacking.

The observed decline and range contraction in both density and occupancy in the Chechen Republic and Stavropol region is due to the rapid replacement of open sands with steppe. This leads to a reduced food supply, as the steppe supports a lower density of lizard populations. In Dagestan, the main limiting factor is the limited availability of sandy massifs with sparse shrub vegetation. In recent years, there has been a decrease in the area of habitats due to excessive grazing pressure. The population is affected by steppe formation, the development of irrigation networks and melon growing (Doronin 2013, Mazanaeva and Orlov 2021).

Globally this species is threatened by habitat loss resulting from intensive agricultural expansion, the abandonment of traditional agricultural areas, overgrazing of vegetation by livestock, mining and drilling operations (oil, salt, mirabilite, sulphur, natural gas), and industrialisation in parts of Middle Asia (including factories and chemical plants).

Live animals of this species occasionally appear in the international pet trade.

This species is listed on Appendix II of CITES. It is included in the Red Data Book of Russia with category and status 2 (Mazanaeva and Orlov 2021). In Russia, the subspecies occurs in at least five reserves and sanctuaries.