Window, Lake Weyba House, Sunshine Coast

Vinyl window to daybed alcove, bedroom pavilion, South-West elevation.

Window, Lake Weyba House, Sunshine Coast

Vinyl window to bath house pavilion, South-West elevation.

Main Pavilion, Lake Weyba House, Sunshine Coast

As seen from West, looking towards front of main pavilion. Standard roller doors to clerestory.

Pivoting vent, Lake Weyba House, Sunshine Coast

Bedroom pavilion, South-East elevation. Day bed alcove on left.

Pavilions and outdoor seating area, Lake Weyba House, Sunshine Coast

As seen from back of bedroom pavilion, looking towards main pavilion. Day bed alcove to bedroom in foreground.

South-West elevation, Lake Weyba House, Sunshine Coast

Bath house and bedroom pavilions, with outdoor seating area in foreground.

Main pavilion, Lake Weyba House, Sunshine Coast

South-West elevation of main pavilion - living, kitchen, dining and study/guest areas.

Bedroom pavilion, Lake Weyba House, Sunshine Coast

As seen from outdoor seating area. Pivoting vent on left and day bed alcove on right. Standard roller doors to clerestory.

Bath house pavilion, Lake Weyba House, Sunshine Coast

South-West elevation. Paved seating area in foreground.

Bath house pavilion, Lake Weyba House, Sunshine Coast

Link to bedroom pavilion on right; roof of main pavilion on left.

North-East elevation, Lake Weyba House, Sunshine Coast

Bedroom pavilion on left, bath house pavilion centre and main pavilion on right.

North-East elevation, Lake Weyba House, Sunshine Coast

As seen from East, looking along pavilions. Bedroom pavilion and day bed alcove in foreground.

Distribution of major, minor, and trace metals in lake environments of Antarctica

The concentrations of major, minor and trace metals were measured in water samples collected from five shallow Antarctic lakes (Carezza, Edmonson Point (No 14 and 15a), Inexpressible Island and Tarn Flat) found in Terra Nova Bay (northern Victoria Land, Antarctica) during the Italian Expeditions of 1993-2001. The total concentrations of a large suite of elements (Al, As, Ba, Ca, Cd, Ce, Co, Cr, Cs, Cu, Fe, Ga, Gd, K, La, Li, Mg, Mn, Mo, Na, Nd, Ni, Pb, Pr, Rb, Sc, Si, Sr, Ta, Ti, U, V, Y, W, Zn and Zr) were determined using spectroscopic techniques (ICP-AES, GF-AAS and ICP-MS). The results are similar to those obtained for the freshwater lakes of the Larsemann Hills, East Antarctica, and for the McMurdo Dry Valleys. Principal Component Analysis (PCA) and Cluster Analysis (CA) were performed to identify groups of samples with similar characteristics and to find correlations between the variables. The variability observed within the water samples is closely connected to the sea spray input; hence, it is primarily a consequence of geographical and meteorological factors, such as distance from the ocean and time of year. The trace element levels, in particular those of heavy metals, are very low, suggesting an origin from natural sources rather than from anthropogenic contamination.

Evolutionary distinctiveness and status of the endangered Lake Eacham rainbowfish (Melanotaenia eachamensis)

The Lake Eacham rainbowfish (Melanotaenia eachamensis) was declared extinct in the wild in the late 1980s after it disappeared from its only known locality, an isolated crater lake in northeast Queensland. Doubts have been raised about whether this taxon is distinct from surrounding populations of the eastern rainbowfish (Melanotaenia splendida splendida). We examined the evolutionary distinctiveness of M. eachamensis, obtained from captive stocks, relative to M. s. splendida through analysis of variation in mtDNA sequences, nuclear microsatellites, and morphometric characters Captive M. eachamensis had mtDNAs that were highly divergent from those in most populations of M. s. splendida. A broader geographic survey using RFLPs revealed some populations initially identified as M. s. splendida, that carried eachamensis mtDNA, whereas some others had mixtures of eachamensis and splendida mtDNA. The presence of eachamensis-like mtDNA in these populations could in principle be due to (1) sorting of ancestral polymorphisms, (2) introgression of M. eachamensis mtDNA into M. s. splendida, or (3) incorrect species boundaries, such that some populations currently assigned to M. s. splendida are M. eachamensis or are mixtures of the two species. These alternatives hypotheses were evaluated through comparisons of four nuclear microsatellite loci and morphometrics and meristics. In analyses of both data sets, populations of M. s. splendida with eachamensis mtDNA were more similar to captive M. eachamensis than to M. s. splendida with splendida mtDNA, supporting hypothesis 3. These results are significant for the management of M. eachamensis in several respects. First the combined molecular and morphological evidence indicates that M. eachamensis is a distinct species and a discrete evolutionarily significant unit worthy of conservation effort. Second it appears that the species boundary between M. eachamensis and M. s. splendida has been misdiagnosed such that there are extant populations on the Atherton Tableland as well as areas where both forms coexist. Accordingly we suggest that M. eachamensis be listed as vulnerable, rather than critical (or extinct in the wild). Third, the discovery of extant but genetically divergent populations of M. eachamensis on the Atherton Tableland broadens the options for future reintroductions to Lake Eacham.