Sternotherus intermedius was historically considered part of the Sternotherus minor complex of turtles. After the description of the subspecies Sternotherus peltifer (Smith and Glass, 1947) and its subsequent placement as a subspecies of S. minor (S. m. peltifer; Tinkle and Webb 1955), many authorities have recognized a presumed area of hybridization/intergradation between S. m. minor and S. m. peltifer (Tinkle 1958, Iverson 1977, Seidel et al. 1981, Ernst et al. 1988). Detailed work by Iverson (1977) clarified the distributions of these two taxa and restricted this zone of integration to gulf-flowing watersheds from the Perdido River to the west to the Choctawhatchee and Econfina rivers to the east. Recent systematic work based upon genomic data (Scott et al. 2018) found that Sternotherus from these watersheds did not represent genetic hybrids between S. m. minor and S. m. peltifer, but were in fact an independent evolutionary lineage, which was described as S. intermedius. In addition, S. minor and S. peltifer were elevated to species by Scott et al. (2018), as they are each monophyletic.

Virtually nothing has been published on the biology, natural history, or demographic trends for Sternotherus intermedius. Much of what is known about this species is either anecdotal from before the species was described, relatively old (30+ years), or both. Superficially, populations seem stable, but this has never been formally quantified. Given this paucity of data and the unknown impacts of habitat degradation and harvest for the pet trade on long-term viability for S. intermedius, a formal status assessment cannot be made at this time. Although the species may potentially be assessed as Least Concern (LC), we assess it as Data Deficient (DD) at this time.

Sternotherus intermedius is found throughout the greater Choctawhatchee and Escambia River drainages including the Perdido, Escambia, Blackwater, Yellow, Econfina, and Choctawhatchee rivers and their tributaries of Florida and Alabama (Scott et al. 2018, TTWG 2021). These watersheds encompass a total of approximately 37,145 sq. km. The species is replaced by S. peltifer to the west in the Mobile/Tensaw watershed and by S. minor to the east in the Apalachicola and Chattahoochee watershed. Additional work is needed to define range boundaries at the interface of the Perdido and Mobile/Tensaw watersheds. The estimated historical indigenous range (area of occupancy, AOO) for the species was 34,785 sq. km, and the estimated historical indigenous extent of occurrence (EOO) was 45,425 sq. km (TTWG in press). The species can be found from at or near sea level along the Gulf Coastal Plain to presumably near the upper elevational limits of the Pea River watershed (tributary of the Choctawhatchee River) at approximately 200 m asl.

No studies have evaluated population sizes, densities, or fragmentation across the distribution of Sternotherus intermedius. In some populations in the Florida panhandle individuals appear to be locally abundant (>2–3 individuals/trap-night; 10+ observations in ca 15 minutes of snorkel survey; P.A. Scott pers. obs.). However, this level of abundance has not been formally quantified, and the association of this abundance with habitat or climatic conditions has not been investigated. Populations of this level of abundance do not appear to be typical and are restricted to high-quality habitat, e.g., spring-run headwaters near the centre of the species' distribution.

Owing to the recent description of Sternotherus intermedius, no studies have explicitly focused on its habitat, ecology, or life history. More work has been conducted on S. minor – particularly from Florida spring systems – and S. peltifer, and presumably much of this information is similar for S. intermedius. Like these other two congeners, S. intermedius inhabits rivers, creeks, spring-runs, freshwater backwaters, bayous, and impoundments (Ernst and Lovich 2009). It may also occur in ponds and lakes in low numbers, but has the highest abundance and trapping captures in free-flowing creeks and spring-runs (P.A. Scott, unpubl. data). Overland movement is likely limited to nesting females. Before the description of S. intermedius, some published studies included life history information for S. minor (sensu lato) from northern Florida, which included populations now known as S. intermedius and S. minor (sensu stricto) (Cox and Marion 1978, Cox et al. 1991). Data for both species is pooled as presented, but presumably accurate for S. intermedius. These studies show S. intermedius has a longevity of 20+ years with the average age at sexual maturity being 5.6 (range 4.4–9.25) years for males and 8 (range 5.6–10.1) years for females (Cox et al. 1991). As such, if we assume sexual maturity at ca 7–8 yrs, then generation time can be estimated as ca 14–17 yrs (Iverson 2024). Southern populations of the S. minor group are likely active year-round in suitable weather conditions (Ernst and Lovich 2009). Sternotherus intermedius has been observed actively foraging in spring run headsprings where water temperatures are consistent (ca 22–24°C) even when air temperature drop below 10°C. The annual reproductive cycle for the S. minor complex in northern Florida is extended (Cox and Marion 1978), with gravid females observed throughout the year except in July and August – potentially indicating a summer recrudescence period. Mean clutch size is 2.4 (range 1–4), where 3–4 clutches/year are common and five clutches/year possible. Clutch and egg size are both correlated with female size (Cox and Marion 1978). Maximum straightline carapace length for males is 11.6 cm and for females is 10.8 cm (J.B. Iverson and P.A. Scott, unpubl. data; TTWG 2021).

Formal threats to Sternotherus intermedius have not been documented, but they are likely similar to those of other river- and stream-dwelling Sternotherus in the southeastern USA. Habitat loss and degradation, including pollution, siltation, and construction of dams and other impoundments all are all likely threats to S. intermedius populations. Trapping success of S. intermedius is lower in impounded and disturbed habitats than less altered ones (P.A. Scott pers. obs.). Degradation of riparian zones is correlated with reduced capture rates of S. minor from Georgia (Sterrett et al. 2010). Incidental capture in crayfish and bait traps may result in accidental drownings – although this is likely relatively rare for this species. Some harvest for the pet trade (including export to Asia and Europe; e.g., Hentschel 2020) likely occurs, but is presumably limited to relatively easy-to-access locations such as bridge crossings and boat launches.

Some Sternotherus intermedius occur in the pet trade (Hentschel 2020). On-line classified advertisements requesting S. intermedius demonstrate the desirability in the trade and some specimens may occur in the pet trade as “S. minor”.

No state or federal protection exists for Sternotherus intermedius. The species was included in CITES Appendix II as Sternotherus spp. in 2023. Both national and state forests as well as numerous water management areas exit within the distribution of S. intermedius and may provide direct (take) or indirect (habitat preservation) conservation management that aids this species.