dc.description.abstract | Microplastics (i.e., plastics particles < 5mm) are widespread emerging contaminants
that have been detected in various aquatic environments worldwide including
freshwater and marine ecosystems. Contamination of the environment with
microplastics has become an environmental issue due to the potential of plastics to
remain for thousands of years and to accumulate in the aquatic environment. The
abundance of microplastics in the aquatic environment is assumed to increase due to
continuous fragmentation of macro and microplastic debris, which can lead to a
decrease in the average size ranges of microplastics over time (Cole et al., 2011).
Moreover, concerns have been raised regarding the potential of microplastics to
physically (e.g., blockage of digestive tract) and chemically (e.g., leaching of sorbed
chemicals and toxic additives) harm aquatic organisms.
Microplastics can enter the aquatic environment from both aquatic-based and landbased
sources. Recently, wastewater treatment plants (WWTP) have been identified
as one of the important land-based sources of microplastics. While microplastics
have been reported in WWTP effluent in Asia, Europe, USA and Russia, little is
known about the presence of microplastics in Australian WWTP effluent. More
importantly, the lack of standardized techniques to sample and characterize
microplastics in environmental samples, especially in complex samples such as
wastewater, has led to inaccurate estimations of microplastic concentrations. In
response to the current knowledge gaps, a novel validated high-volume sampling
device was developed for in situ fractionation of microplastics from wastewater
effluent as part of this project. The developed method was applied to three Australian
WWTPs utilizing primary, secondary and tertiary treatments to provide a snapshot of
the fate and removal of microplastics during various wastewater treatment processes.
To achieve an accurate estimation of microplastics, the sampling technique was
combined with an efficient sample processing method. Microplastic polymer type,
shape and potential origin were further determined using microscopy analysis and
Fourier Transform Infrared (FTIR) spectroscopy. The efficiency of the sampling
device was found to be between 92 to 99% for 500 and 25 μm mesh screens. The
results showed that the concentrations of microplastics were 1.5, 0.6 and 0.2
microplastics per liter of effluent in primary, secondary and tertiary effluent,
respectively. It was also found that the majority of detected microplastics in the
studied WWTPs were polyethylene terephthalate (PET) fibers, which is assumed to
originate from synthetic clothing. Polyethylene (PE) beads and fragments, which may be associated with cosmetic products, were the second most frequently detected
type of microplastic. Despite a thorough sample processing method, FTIR
spectroscopy revealed that between 22 to 90% of the suspected microplastic particles
were in fact non-plastic particles. This study suggests that WWTPs can act as a
significant source of microplastics to the aquatic environment given the large volume
of wastewater discharged to the aquatic environment.
To date, the effects of microplastics on aquatic organisms have mostly been
examined using high and often unrealistic concentrations of microplastics (e.g.,
milligram per liter range). Moreover, while the presence of different types of
microplastics together in aquatic ecosystems has been widely reported, the potential
effects of microplastics when they occur as mixtures are largely unknown. To cover
these knowledge gaps, the potential adverse effects of wastewater-based
microplastics (such as fibers and beads) at lower concentrations on the freshwater
organism Ceriodaphnia dubia were evaluated. The acute (48 h) and chronic (192 h)
effects of PET fibers and PE bead microplastics on C. dubia were assessed alone and
as a binary mixture. The results showed a dose-dependent trend on survival, with C.
dubia more sensitive to PET fibers than PE microplastics. The 48 h EC50 value of
fibers was 1.5 mg/L compared to 2.2 mg/L for PE beads. The binary mixture of
microplastic beads and fibers demonstrated less than additive effects. EC50 values for
the chronic bioassay were 429 μg/L for fibers and 958 μg/L for PE microplastics. A
positive trend of decreasing growth (body size of adults) and reproduction rate
(number of neonates) with increasing microplastic concentration was observed for
both PE and fiber microplastics during the chronic bioassays. Using scanning
electron microscopy (SEM) we observed deformities, such as carapace and antenna
deformation, in C. dubia exposed to fibers at a high concentration, but not at the
lower (environmentally relevant) concentrations.
Given the likelihood that microplastics will eventually sink to the bottom sediment in
the aquatic ecosystem the effects of microplastics were investigated on a freshwater
sediment-dwelling organism (Chironomus tepperi) at environmentally relevant
concentrations of PE microplastics (500 particles/kgsediment). Possible size-dependent
effects of microplastics were also examined using four different size ranges of PE
beads including 1-4, 10-27, 43-54 and 100-126 μm. The results revealed that
exposure to an environmentally relevant concentration of microplastics had a
detrimental impact on the survival, growth (i.e., body length and head capsule) and
emergence of C. tepperi. The observed effects were strongly dependent on microplastic size with C. tepperi more sensitive to microplastics in the size range of
10-27 μm. No negative effects were observed on growth and survival of C. tepperi
exposed to the larger microplastics (100-126 μm), though a significant decrease in
the number of emerging adults was observed in the organisms exposed to the same
size range of microplastics. Further, SEM showed a significant reduction in the size
of the head capsule and antenna in C. tepperi exposed to microplastics in the size
range of 10-27 μm. These results showed that environmentally relevant
concentrations of microplastics in sediment can result in adverse effects on the
development and emergence of C. tepperi, with effects strongly dependent on
particle size.
Finally, we evaluated the effects of PE microplastics on the acute toxicity of a
pyrethroid insecticide (bifenthrin) to midge larvae (C. tepperi) in water. To test the
single and combined effects of bifenthrin and PE microplastics, C. tepperi larvae
were exposed to six concentrations of bifenthrin ranging from 0.1 to 3.2 μg/L in the
presence and absence of microplastics. To examine the possible effects of bifenthrin
and microplastics in synthetic and real water, the bioassays were performed in both
moderately hard water (MHW) and river water. We performed an uptake study using
three different size ranges of microplastics (10-27, 43-54, 100-126 μm) during 8-day
microplastics-spiked water exposure. The results showed that microplastics in the
size range of 10-27 μm were mostly ingested by C. tepperi larvae. Using this finding,
10-27 μm microplastics were selected for the bioassays. The results of the bioassays
using MHW demonstrated a significant decrease in the toxicity of bifenthrin in the
presence of microplastics. This is likely attributable to the tendency of bifenthrin to
bind to the microplastics, which reduces the bioavailability of bifenthrin to midge
larvae. However, in the bioassays conducted in river water with a total organic
carbon (TOC) concentration of 9.6 mg/L, no significant difference was observed
between the toxicity of bifenthrin to C. tepperi in the presence and absence of
microplastics. This is likely due to the interaction between organic carbon and
bifenthrin, which reduces the bioavailability of bifenthrin to C. tepperi larvae.
This thesis highlights that microplastic fibers and beads are released to the aquatic
environment from WWTPs, and that this can negatively affect survival, reproduction
and the life cycle of aquatic organisms (both pelagic and benthic) through
entanglement (fibers) and ingestion (beads). The effect of microplastics on chemical
contaminants is complex, and microplastics may act both as carriers but also as
“chelators” of chemicals in the water, thereby reducing their bioavailability. | |