Received in revised form 6 January 2020 species exposure to metal contaminants, nor their ability to uptake and translocate metal(loid)s from contaminated

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are between 25 and 50% of their historical distribution (Mcowen et al., Klink, 2014; Zhang et al., 2014). There are, however, a few grass repre-
2017), while in Australia over 50% of wetlands have been modiﬁed or sentatives which deviate from this pattern, and have been found to
mean that threats and impacts to the vegetation community are man- couch, is a monocotyledon in the Family, Poaceae. It is a C4 perennial tus-
et al., 2007; Nath et al., 2013, 2014). Resultant metals in estuarine sedi- eries productivity in SE Australian estuaries. Through stable isotope
of metals with negatively charged Si-dominated clay matrices, binding to consumer diet (25–95%) compared to other saltmarsh species, man-
utable to the variably anoxic nature of sediments (Harbison, 1986; Despite its importance as a primary producer, little prior research
a 50% decline in growth (EC50), ranges from salinities of 150 mM in with dose) at key potential cellular and molecular roadblocks in transi-
dependent assessment of spatial variability in metal load (n = 45 total).
1995 operating procedures were updated, with dam water recycled particle size ranges were gravimetrically determined following oven
elevated predominantly in Se and Cd (Carroll, 1999; Peters et al., SOM (%) = TOC (%) ∗ 1.72 (assuming that organic matter contains
1999; Schneider et al., 2014). Swansea is located at the marine entrance 58% organic carbon). To determine TOC, b2 mm sediment was placed
Sydney. The original wetland complex was reclaimed for industrial de- EC from 0.01 to 2.6 (μS/cm) and SOM 0.5 to 30.5% among locations.
iment was dredged from Homebush Bay to create an elevation suitable homogenised sediment sample was taken and 5 mL of aqua regia
the following temperature program: 70 °C for 30 min, 90 °C for The standard reference materials, marine sediment (PACS−2; N =
gestion block and allowed to cool to room temperature prior to dilution methods, respectively (Table 1). Trace metals are usually associated
with 0.1% nitric acid (20 mL). The samples were transferred to tubes and with the ﬁnes of sediments, dominated by clay and Fe and Mn
and estuary sediment metal differences (Suh and Birch, 2005). Sedi- mium ranged from 0.18 ± 0.05 μg/g at Dora Creek, Lake Macquarie,
whether metal(loid) loads in sediments posed toxic risk to associated tion. Selenium concentrations were low and ranged from 0.14 ±
1. were included for comparison (Table 2). decommissioned Pb/Zn smelter in Lake Macquarie consistently exhib-
Dimensional Scaling (nMDS) ordination employing Euclidian distance was extremely elevated at Five Islands) (Table 2).
to roots, patterns of translocation between organs with increasing metal blages (Pseudo F = 46.2, p = 0.001) (Table 3). Turning to Fe-
accumulation from sediment to roots, multiple regressions were also (Table 3). Pairwise post-hoc tests revealed all estuaries were signiﬁ-
employed in IBM SPSS Statistic 24. Signiﬁcance was assessed at the 5% cantly different from each other in terms of Fe-normalised metal(loid)
individual plant then averaged across sites (n = 45).
values. Similarly, Cu ranged from 2.1 ± 0.2 μg/g at Coon Island, Lake between plant organs, Zn in culms increased as root Zn increased
1. Dora Creek Mean 14.29 6.94 32.64 0.18 1.14 18.76 6.27 10.58 0.22 0.71 21.43 3.56 2.26 0.08 0.19 13.93 6.98 1.03 0.01 0.09
6.Haslam’s Flats Mean 55.96 11.34 36.64 0.64 0.90 40.82 24.09 12.75 0.62 0.23 43.85 27.43 1.86 0.38 0.11 30.09 16.45 0.91 0.21 0.08
explaining variation in root Zn (Table 4).
sediment was around unity (TF = 0.89), while strong barriers to trans- duced translocation at approximately 50% of the previous compart-
linity on Pb uptake (Table 4). cumulation to roots (Table 4).
Table 4 Relative metal loading ranks among these three estuaries observed
(N = 44 for Zn, N =45 for all other metal(loid)s). across 38 estuaries in SE Australia, which represent the normalised sur-
ground concentration. Mean enrichment for Cu, Pb and Zn were 6.7,
EC 0.062 0.738 0.465 utable to coal-ash associated sources from the coal-ﬁred power stations
SOM % −0.002 −0.332 0.742 in this vicinity. This largely reﬂects trends observed in sub-tidal sedi-
clay % −0.001 −0.437 0.665 vated in Cd, Pb, Hg, Se, Ag and Zn, while the south of Lake was elevated
SOM % −0.007 −0.726 0.472 the Lake, a trend in declining metals (especially for Pb) has been ob-
clay % 0.000 0.171 0.865 tion observed in the present study (Cu 2–39 μg/g, Pb 8–417 μg/g, Zn
clay % −0.001 −0.596 0.555 in Lake Macquarie (Cu 1–81 μg/g, Pb 3–1497 μg/g, Zn 20–563 μg/g, Cd
0.019) (Table 4). lands. Ranges of metals in the current study i.e. Cu (5–12 μg/g), Pb
1. Discussion at similar locations on the Island, likely attributable to spatial heteroge-
culm concentrations approximately 50% of root loads. Transport be- number of simultaneous comparisons among metal(loid) candidates.

Methods (brief)

metal gradient in order to assess metal transport in the plant and rela- A total of four locations were sampled in Lake Macquarie, three loca-
1. What is the sediment metal(loid) contamination status of 2.2. Sampling design and sample preparation
New South Wales (NSW), Australia? Within each of the 9 locations, plants and sediment were collected at
was to ensure separate individual plants were sampled and to allow in-
At each site, one mature plant (or sample of a plant, as S. virginicus
typically descend into the sediment proﬁle) was collected adjacent to
the plant using an aluminium trowel. Samples were placed on ice in
oratory. Plants were sampled from monospeciﬁc stands of S. virginicus
2.1. Study locations growth, all locations were sampled between the 5th of May and 28th
of June 2019. Upon return to the laboratory, random subsamples from
sphere. Lake Macquarie has a long history of industrial development and stored at −20 °C until further analysis. Rhizomes were not sampled
smelting facility (now decommissioned) and three coal-ﬁred power samples were later oven dried at 60 °C and then ground to a ﬁne powder
Northern end of the lake, was the Pasminco Pb/Zn Smelter, which oper- providing homogenous samples. Sediment cores were stored at
The Hunter Estuary, Hunter Wetlands National Park (Kooragang Is- with mortar and pestle. A 0.5 g sample of sediment was treated with
remediating with clean topsoil. The Badu saltmarsh, located in Bicen- Samples of b2 mm sediment from each entire core were oven dried
iment was dredged from Homebush Bay to create an elevation suitable homogenised sediment sample was taken and 5 mL of aqua regia
for saltmarsh colonisation. (HNO3/HCL: 1:3, ICP-MS grade, Merck) was added in Teﬂon digestion
digestion system (model: MARS 6, CEM, USA) following the US EPA using an Agilent 7900 (Agilent Technologies, Tokyo, Japan) inductively

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The five most recent substantive edits to this page, classified major (evidence or structure moved), correction (a published value or statement was wrong and has been fixed), or minor (narrative rewritten without changing the underlying evidence). Each description is derived from what the edit did to this page; the linked commit is the authoritative record, routine regeneration passes are excluded, and the full version history lives in git. When DOI minting comes online (see schema docs), each entry below will also link to a version-pinned DataCite DOI.

Commit	Date	Change	Description
b01ec52c	2026-08-04	major	2 sections added
d49e450f	2026-08-03	major	5 sections added; narrative text revised