The Negative Effects to Prevalent Plastic Pollution

By Delaney Reynolds, SRC intern

Plastic pollution has become one of the largest adverse impacts on marine life to date. In the last 70 years, plastic debris has become so prominent in layers of sedimentary deposits that it can be used as a primary indicator for the Anthropocene, a human-induced geological epoch (Puskic, et al. 2019). While plastic does technically break down, it only fragments into micro- and nano-plastics and thus never leaves the environment completely. These miniscule particles are commonly consumed by marine animals of all sizes ranging from plankton to whales. Seabirds such as albatross, petrels, and shearwaters have been found to have very high plastic ingestion rates due to their foraging strategies, as well as its various colors and odors that they find attractive. Ingesting plastic debris causes damage to lipid-derived fatty acids (FAs). FAs are warehoused in a variety of tissues for energy storage. Adipose tissues, connective tissue that also stores energy in the form of fat, contains triglycerides (TAG), main constituents in body fats, which are a vital energy source for juvenile birds.

Figure 1: Plastic pollution in Guanyin District, Taiwan (Source: Henry & Co. on Unsplash: https://unsplash.com/photos/cZpvuwwQQg0)

Researchers from the Institute for Marine and Antarctic Studies at the University of Tasmania explored how FA analysis could be used to investigate the impacts of seabird plastic ingestion on seabirds’ health. Roadkill or beach-washed deceased flesh-footed shearwater and short-tailed shearwater fledglings were collected on Lord Howe Island, New South Wales, Australia. Their body mass, wing length, and head + bill length were measured and plastic debris less than one millimeter in size were weighed. Adipose tissues were collected from breasts and FAs were extracted and analyzed with several statistical tests. The average number of plastic debris ingested was found to be 4.47 pieces weighing approximately 0.0760 grams for short-tailed shearwaters. The average number of plastic debris ingested was found to be 18.44 pieces weighing approximately 2.9277 grams for flesh-footed shearwaters. Although the research did not find a significant relationship between the mass of plastic, number of plastic debris present, and body mass, 37 different FAs were found in liver and muscle tissues between both species (Puskic, et al. 2019).

Figure 2: Differences in fatty acids between flesh-footed shearwater and short-tailed shearwater seabirds (Source: Puskic et al. 2019).

Discrepancies found between the FAs identified in the different species of shearwaters may be attributed to the turnover rate of FAs and lipid classes specific to tissues. The study concluded that flesh-footed and short-tailed shearwaters are, indeed, two distinct groups of one species based on FA composition. The FA composition of prey species likely drives the difference, as flesh-footed shearwaters are known to feed on mesopelagic fish and squid and short-tailed shearwaters are known to feed on krill and small cephalopods. These two different classes of prey have dramatically different FA levels, and this was found to be reflected in the FA outputs of the two different shearwaters.

Based on this study, fatty acid analysis can be used to explore how plastic pollution disrupts nutritional pathways and it was found that within the sample of shearwaters collected, there was no effect. These types of studies and tools will be imperative for use to manage and analyze the current and future effects of plastics on other species, especially marine, as anthropogenic-driven plastic pollution continues to become more prevalent in our world.

Works Cited:

Puskic, Peter S, et al. “Uncovering the Sub-Lethal Impacts of Plastic Ingestion by Shearwaters Using Fatty Acid Analysis.” Conservation Physiology, Oxford University Press, 16 May 2019, academic.oup.com/conphys/article/7/1/coz017/5489824.

Endangered Atlantic Sturgeon in the New York Wind Energy Area: implications of future development in an offshore wind energy site

By Enzo Newhard, SRC intern

The environmental benefits of renewable energy sources have been well established as the “pro green” discourse emphasizes the importance of eliminating our input of greenhouse gasses into the environment. The negative impact renewable energy development may have on the environment, however, has not been as thoroughly discussed. Burning fossil fuels releases harmful gasses into the atmosphere adding to the greenhouse effect and alters global ecosystem chemistries. Renewable sources’ generally have no waste product but due to their lower efficiency the installations need to take up a much larger area. However, it is largely unknown how some of these instillations could impact the environment in which they are installed especially ones in the ocean. A paper by Evan Corey Ingram, Robert M. Cerrato, Keith J. Dunton, and Michael G. Frisk, titled Endangered Atlantic Sturgeon in the New York Wind Energy Area: implications of future development in an offshore wind energy site, lays the groundwork for assessing the disturbances the development of an offshore wind farm may have on local populations of Atlantic Sturgeon.

The Atlantic Sturgeon is an endangered anadromous fish which is the species of concern for this paper as it is believed to be present in the waters slotted for the development of the New York Wind Energy Area (NY WEA). 133 Atlantic Sturgeon were caught and fitted with acoustic transmitters to record and track their movements in the WEA. Sturgeon were regularly detected throughout the study period except from July-September when abundance was low. Both temporal and spatial variations in their distribution were observed with the majority of detections occurring at the nearshore receivers except for periods of high abundance where the fish seemed more uniformly distributed throughout the WEA (Ingram et. al. 2019).

Figure 1. “Detection count (top panel) and unique transmitter count (bottom panel) of Atlantic Sturgeon detected on acoustic transceivers in the New York Wind Energy Area study site (Equinor, Lease OCS-A 0512). Transceivers are represented by increasing distance from shore; note that intervals are not equal.” (Source: Ingram et al. 2019)

Most of the research regarding sturgeon stocks has been done in riverine and estuarine environments, information about their population dynamics and foraging ecology in marine environments is largely unknown. This study provided a valuable baseline of sturgeon distribution and abundance in the future wind energy site and underscores the importance of long-term monitoring of offshore areas to enhance recovery efforts by locating important new habitats which have been underrepresented in current scientific literature.

Figure 2. “Monthly counts of unique Atlantic Sturgeon (represented by graduated symbols) detected at unique acoustic transceiver stations in the New York Wind Energy Area study site (Equinor, Lease OCS-A 0512) from November 2016 through January 2018. Monthly point values of average bottom temperature were compiled from transceiver metadata. The transceiver array operated throughout the entire course of the study with the exception of a single station indicated by (^) which was not recovered during the final download cruise; data for this station were unavailable for the months of August 2017–February 2018” (Source: Ingram et al. 2019)

Work Cited

E.C. Ingram, R.M. Cerrato, K.J. Dunton, M.G. Frisk 2019. Endangered Atlantic Sturgeon in the New York Wind Energy Area: implications of future development in an offshore wind energy site. Scientific Reports 9:12432

Migrating eastern North Pacific gray whale call and blow rates estimated from acoustic recordings, infrared camera video, and visual sightings

By Bella Horstmann, SRC intern

Previously almost hunted to extinction, the North Pacific gray whale population currently inhabits the waters off the coast of California. Distinguished by their extremely long and predictable migration patterns, these animals have been observed very close to shore, making them a model species for studying population dynamics and animal abundance because of the ability to easily spot from land. During the 2014-2015 southbound migration period, a group of researchers from the National Oceanic and Atmospheric Administration (NOAA) and the Scripps Institution of Oceanography sought to understand these population dynamics and statistically estimate cue rates by using visual sightings, combined with acoustic call recordings, and infrared blow detections. Each year during December through March, these charismatic marine mammals migrate between summer feeding areas in the Bering and Chukchi Seas, and the wintering areas of the lagoons in Baja California Peninsula in Mexico. Past studies on population abundance have just included visual surveys from land or on a ship, which can be time intensive, expensive, and may introduce the confounding variable of human impact. Here, Guazzo et. al (2019) turned to autonomous techniques in hopes of revealing a more reliable and accurate methodology for population abundance estimates.

Owing to their proximity to land, North Pacific gray whales can be visually surveyed from the Granite Canyon study site, an area where the continental shelf is particularly narrow, making for simple visual detection from land. Observers stood 22 meters above sea level and recorded gray whale sightings for 34 days during December 2014 and February 2015. Additionally, four hydrophones were moored to the bottom of the ocean in different locations in between November 2014 and June 2015, and continuously collected acoustic information throughout the whole migration season. Lastly, three infrared cameras pointing at different angles offshore recorded blow detection. In Figure 1, which is a map of the study area for the combined surveys, the location of the NOAA visual observers, as well as the location of hydrophones and infrared cameras is indicated.

Figure 1. Map of study area. The black circle indicates where the visual observers stood on land. The yellow lines show the visual field of these observers. The white diamond indicates where the infrared camera, and the pink lines show the window of detection for that camera. The four black triangles indicate the locations of the four underwater hydrophones and are labelled accordingly. Color indicates elevation and depth. (Source: Guazzo et al. 2019)

Once the southbound migrating North Pacific gray whales were detected, a cue rate formula was utilized in order to get an accurate population abundance estimate. Using all of the combined methods, a population of 38,304 whales was estimated to migrate during the 2014-2015 season. The acoustic findings showed an interesting daily call rate increase from 5.7 calls/whale/day to 7.5 calls/whale/day, indicating an increase in communication during the migration season. Figure 2 shows the gray whale tracks from the visual, acoustic, and infrared localizations.

This paper is unique because it monitors population abundance using cue rates, a technique that minimizes confounding variables and human impact on the animals. Using these combined techniques also increases the accuracy of the results due to an increased sample size. This is a huge step in the world of marine mammal research, as this combined methodology can be applied to other marine mammal studies, in hopes of more accurately tracking population densities and sizes.

Figure 2. Example North Pacific gray whale tracks from combined methodology localizations. The colored circles indicate visual sightings, and the colored triangles indicate acoustic calls. Infrared blow detections are shown by the colored diamonds. The color variation indicates the amount of time in minutes since the start of the detection. As in Figure 1, the black triangles are the presence of the hydrophones, the pink lines are the infrared detection area, and the yellow lines are the visual field of the observers onshore. (Source: Guazzo et al. 2019)

Works Cited

Guazzo, R. A., Weller, D. W., Durban, J. W., Gerald, L. D., & Hildebrand, J. A. (2019). Migrating eastern North Pacific gray whale call and blow rates estimated from acoustic recordings, infrared camera video, and visual sightings. Scientific reports9(1), 1-11.

Securing Sustainable Somali Fisheries

By Peter Aronson, SRC intern

Lots of people know about the issue of piracy in Somali waters in recent years, with mass coverage from American media and even Hollywood focusing on it with the 2013 movie Captain Phillips. However, many people don’t know that the loss of secure fisheries to illegal foreign vessels was the root cause of these conflicts (Beri, 2011). In the 1980’s, when the Somali Civil War first broke out, the central government collapsed and the Somali Navy disbanded. As a result, foreign fishing boats took advantage of the lack of security and fished Somali waters heavily, leading to great erosion of fish stocks. With no government intervention to help, artisanal Somali fishermen banded together to protect their own resources. At first, violence was not threatened or used. However, as events escalated, weapons were used, both poor fishing vessels and wealthy cargo vessels were taken over, and in some cases hostages were held for ransom. As this became profitable, pirate activities became widely funded by financiers and militiamen on land. The cause of all this was illegal foreign fishing.

Illegal, unreported, and undocumented (IUU) fishing from foreign fleets declined in Somalia in the mid 2000’s due to piracy, but increased again when foreign naval fleets began patrolling Somali waters to reduce piracy (Oceans Beyond Piracy, 2014). Seeing foreign fleets off the coast angered the public and increased support for piracy, as sustainably developing artisanal and subsistence fisheries became much more difficult with pressure from foreign operations. Due to uncertainty of the legality of foreign fishing for decades, unregulated fishing with ineffective enforcement of decades-old policy, and catch that hasn’t been reported to the United Nations since 1988, there is a widespread perception that any foreign fishing activity in Somalia is illegal (Glaser et al., 2015).

Apart from poor fisheries management, there is justified anger towards foreign vessels due to violent conflict. They have been accused of hiring armed guards to shoot at Somali fishers, blasting hot water at Somalis, and destroying fishing gear in domestic artisanal fisheries (Glaser et al., 2015). Additionally, Somalis are upset at the foreign fleets’ destruction of fish stocks at the expense of domestic fishing, and using destructive methods, such as bottom trawling, that destroy coral reef and other habitat. As a result, Somalia has removed fishing rights from many foreign vessels, and have even captured vessels and imprisoned the fishermen aboard them (Glaser et al., 2015).

Using satellite data, the Secure Fisheries group with the One Earth Future Foundation estimated the amount of foreign fishing vessels in Somali waters between 1981 and 2013, and the amount of fish they took. It was estimated that 3.1 million metric tons of marine life was taken in this time frame by foreign vessels, more than twice the amount that domestic Somali fishermen took at 1.4 million metric tons. The heaviest fishing nations in the time frame are Iran, Yemen, Spain, Egypt, and France, though in 2013 Spain, Seychelles, France, South Korea, and Taiwan dominated.

Trawling has had a great impact on Somalia’s marine habitat. Trawling from foreign nations continued for decades following the collapse of Somalia’s government, with bottom trawling even continuing beyond Somalia’s ban of it in the new Somalia Fisheries Law. It was mainly Italian and Egyptian vessels trawling until 2006, when South Korean ships replaced the Italian ones. Italian and Korean vessels fished 220 and 229 days of the year respectively. Some trawlers are actually licensed to Puntland, a coastal region in Somalia on the Horn of Africa. Due to its wide continental shelf and high fish availability, as well as licensing in the region, most trawling occurred in shallow waters here. Over the time period that data was collected, 120,652 square kilometers were trawled, an area slightly larger than the neighboring nation Eritrea (Glaser et al., 2015). This doesn’t account for areas of seafloor that were trawled multiple times. Several areas that experienced this underwent significant ecosystem damage.

In Somalia, foreign fleets are larger, better equipped, and more technologically advanced, giving them a competitive edge over smaller Somali vessels. Globally there is a similar trend of large, distant, industrial fleets outcompeting small, artisanal and subsistence fishers. These small-scale fishers are some of the world’s poorest people and are extremely vulnerable to changes in resource availability (Béné, 2009). The current sustainability of fish stocks were estimated by Secure Fisheries using methods designed for data-poor fisheries. It was found that 8 of 17 fish groups analyzed are currently fished unsustainably, including swordfish, emperors, sharks, snappers, and groupers. This data must be used cautiously, as categories were analyzed at different levels, such as striped marlins at the species level, to sharks at the family level. Additionally due to little available data, estimations of migratory species used catch reconstruction and the classification of whether or not a stock was sustainable was based on comparison to an exact calculated value.

Optimistically, a lower proportion of fish stocks are being fished unsustainably in Somalia than globally, and no stocks are collapsed whereas 24% of stocks are globally. This advantage is due to delayed industrial fishing in Somali waters. However, if trends continue and follow the preceding global pattern, it is estimated that over half of Somali stocks will be overexploited by 2025 (Glaser et al., 2015). It is important to move towards sustainable fisheries in Somalia. With the full effects of postcolonialism pressing down on the nation, sustainable fisheries could promote the Somali economy, provide food, and nourish many for years to come.

Works Cited

Béné, C. (2009). Are Fishers Poor or Vulnerable? Assessing Economic Vulnerability in Small-Scale Fishing Communities. Journal of Development Studies, 45(6), 911–933. doi:10.1080/00220380902807395

Beri, R. (2011). Piracy in Somalia: addressing the root causes. Strateg. Anal., 35 (3), 452-464.

Glaser SM, Roberts PM, Mazurek RH, Hurlburt KJ, and Kane-Hartnett L (2015) Securing Somali Fisheries. Denver, CO: One Earth Future Foundation. DOI: 10.18289/OEF.2015.001

Oceans Beyond Piracy. (2014). The State of Maritime Piracy Report 2014. Denver, Colorado: One Earth Future Foundation.

The transfer of energy within a food chain: Why do large whales feed on small plankton?

By Meagan Ando, SRC intern

The ten-percent rule toward energy transfer among levels of a trophic system is one that has been used to study ecosystems’ energy dynamics for a long time. But, in order to understand it, one must have a basic understanding of a food chain (Figure 1). Food chains describe the transfer of energy from its source in plants, through herbivores, up to carnivores and onto higher order predators (Sinclair et al. 2003). These different “levels” are known as trophic levels, which is properly defined as the position within the food chain or energy pyramid that an organism can be found. But how much energy is passed along through each level? This is where the ten-percent rule comes in.

Figure 1: An example of a food chain. The first trophic level consists of primary producers gathering energy from the sun, which will be passed up to herbivores, then multiple levels of carnivores (source: nau.edu).

Food webs are often pretty short, which confused many scientists for a long time. Ever wonder why such a large whale feeds on such small planktonic organisms, such as krill? The evidence for the evolutionary advantage of this strategy lies within the definition of the ten-percent rule. When energy is passed along throughout an ecosystem from one trophic level to the next, only 10% of the energy that the first organism receives will actually be passed along. The way in which to study this phenomenon has certainly presented it’s difficulties, as it is clearly impossible to actually visualize the transfer of energy. However, the primary means for determining what marine organisms eat is to study their stomach contents, which is exactly what Reilly et al. 2004 did.

It was known that the International Whaling Commission (IWC) along with the Commission for the Conservation of Antarctic Marine Living Resources (CCAMLR) shared a common curiosity in the idea of the feeding ecology of Baleen whales. This was significantly due to their interests in efforts to place management decisions within an ecosystem context (Reilly et al. 2004). The most efficient way for them to determine their prey sources was to estimate krill consumption by various species of Baleen whales in the Southern Atlantic region during the summer feeding season in the year 2000. In order to successfully draw these estimates, inferences had to be made pertaining to how frequently the whales actually filled their stomachs. This included diurnal change in the forestomach content mass, which ended up producing estimates of 3.2-3.5% of body weight per day (Figure 2) (Reilly et al. 2004). To follow through with the energy tests, four ships participated in the survey to weigh the stomach contents of whales that were unfortunately killed for commercial or research whaling.

Figure 2: Daily consumption rates determined by the four models pertaining to various baleen whales (Humpback, Fin, Right, Sei, and Blue) (Reilly et al. 2004).

In total, 730 cetacean sightings were recorded which included 1,753 separate individuals. It was determined that 83% of the annual energy intake for the whales in this region occurred during this
120-day feeding span in the summer season. The range of total consumption was 4-6% of the standing
krill stock (Reilly et al. 2004). This percentage was derived from the fact that the initial stock included approximately 44 million tons of krill, of which the whales consumed somewhere between 1.6 million and 2.7 million tons (Reilly et al. 2004). These numbers allowed the scientists to make connections between food consumed and the total amount of energy a whale needs to carry out daily bodily functions to survive. It also allowed them to draw conclusions based on where they feed to better protect threatened animals as well as to tweak quotes set for the commercial exploitation of krill, as it is their main food source.

With all of this in mind, it still may not make sense as to why such a large animal would feed on some of the smallest organisms in the ocean. Blue whales, which can be 20-30 meters long, feed on shrimp-like krill that are a mere 2-3 centimeters long. As stated above only ten percent of the energy obtained from one trophic level gets passed along to the next trophic level. For this reason, ecosystems with longer food chains are proven to be, on occasion, less stable than those whose food chains are shorter (Sinclair et al. 2003). Therefore, it is more advantageous for the whale to eat animals on a trophic level in which there is more energy available to be taken in. Hill et al. 2018’s textbook Animal Physiology describes this concept in more depth. In it, they contrast two different possible mechanisms by which a whale can obtain food. One is for the whale to eat fish that are somewhat smaller than themselves. These fish can potentially eat fish that are slightly smaller than themselves, and so on. In this case, there are many trophic levels that the energy will have to pass through before reaching the whale. To apply the ten percent rule directly, we can say that the primary producer produces 10,000 units of energy obtained from the sun. The crustaceans that feed on the producer will generate 1,000 units of energy, from which the small fish that feeds on them will produce only 100 units of energy. The larger fish that feeds on this fish will produce only 1 unit of energy, which may not be enough to sustain the large whale. This is why Baleen whales have evolutionarily evolved into suspension feeders, using Baleen plates to take in large amounts of water and sift through to find small krill. The Baleen whales can eat organisms much smaller than themselves, which can cut down the trophic levels between primary producer and the whale itself, making the energy available to the whale population 1,000 units, as opposed to only 1. In summation, shortening the food chain will in turn increase the food energy available to the whales by a factor of 1,000 (Figure 3) (Hill et al. 2018).

Figure 3: Shorter food chains deplete the energy available to whales less that longer food chains. (Hill et al. 2018).

By better understanding the way in which whales, or any animal for that matter, obtains energy through food, we can further implement new methodologies to better protect them. For example, now that it is known that krill play an extremely important role in the survival of the Blue Whale, agencies can implement new ecological management strategies to be sure that krill populations are not significantly affected by anthropogenic impacts. They may seem like invisible creatures floating in the ocean, but to Baleen whales, they mean a whole lot more.

Works cited

Hill, Richard W., et al. 2018. Animal Physiology. Sinauer Associates/Oxford University Press. Nau.edu. “Life on the Food Chain.” The Food Chain.

Reilly, S., Hedley, S., Borberg, J., Hewitt, R., Thiele, D., Watkins, J. and Naganobu, M., 2004. Biomass and energy transfer to baleen whales in the South Atlantic sector of the Southern Ocean. Deep Sea Research Part II: Topical Studies in Oceanography, 51(12-13): 1397-1409.

Sinclair, Michael, and G. Valdimarsson. 2003. Responsible Fisheries in the Marine Ecosystem. Food and Agriculture Organization of the United Nations 8: 125-131.

Loss of North American Freshwater Biodiversity

By Chris Schenker, SRC intern

Despite garnering less attention than their marine counterparts, freshwater species are diverse, important, and also under threat. Despite covering only 0.8% of the world’s surface and accounting for about 0.01% of the world’s water, freshwater contains at least 100,000 distinct species (Dudgeon et al. 2006). Comparisons to other environments are difficult because of the variation surrounding estimates of the total number of species on Earth. However, given freshwater’s disproportionately small share of total volume and surface area, it is beyond doubt to assert that its species density is staggeringly high. Although the interrelationships are not completely understood, freshwater biodiversity plays a crucial in ecosystem function as a whole. Despite the value that freshwater flora and fauna add from a scientific, commercial, aesthetic, cultural, and recreational perspective, the species extinction rate is far higher than that for their terrestrial counterparts (Dudgeon et al. 2006).

Figure 1: Freshwater fish are under threat worldwide, but the trend is especially pronounced in North America. (Unsplash.com)

This dynamic is especially clear in North America, where aquatic environments are well-studied. Although freshwater biodiversity is higher in the tropics, North America has the highest nontropical species diversity (Lundberg et al. 2000), totaling 1,213 as of 2010 and accounting for 8.9% of the world’s freshwater fish species (Nelson et al. 2004). There is a long history of species documentation in North America, with the first observed extinctions occurring in the early twentieth century. Since then, 39 species of North American freshwater fish have been declared extinct (IUCN 2011), yielding a continental extinction rate of 3.2% (Burkhead 2012). This is a higher total than is observed globally, but that is only because of North America’s longer history of continuous faunal study in comparison to the tropics. Regions with similar histories of scientific documentation display similar trends, with 3.4% of species considered extinct in Europe (Freyhof and Brooks 2011), and 3.2% of species considered extinct in the European basin (Smith KG and Darwall 2006).

The metric that really matters is the modern extinction rate in comparison to the background extinction rate. The background extinction rate, often abbreviated BER, is the taxonomic extinction rate over geologic timescales before the introduction of human pressures. Knowing both values allows scientists to calculate the ratio of modern extinction rate to background extinction rate (M:BER). There are difficulties in calculating both rates, so numbers should be interpreted with a grain of salt, but this ratio gives a rough estimate of how much faster extinction is occurring due to humanity’s global remodeling. The M:BER ratio for North American freshwater fishes has been calculated to be as high as 877 (Burkhead 2012), making it the highest number for any contemporary vertebrate group (Barnosky et al. 2011). Despite the large number of estimates and assumptions underlying this number, it highlights the severity of the problem species are facing. Fishes labeled as threatened, endangered, and declining will be subjected to the most intense pressure, especially those that are endemic and lie in the path of future human expansion.

Figure 2: This table compares the modern extinction rates for world vertebrates to their estimated background extinction rates. (Burkhead 2012)

As imperiled as freshwater fishes are, they are only the beginning when it comes to declining freshwater flora and fauna. Many molluscs, such as snails and mussels, are going extinct at a rate that is an order of magnitude greater than that of freshwater fishes (Burkhead 2012). The main cause of this plight is human alteration of rivers and lakes, along with runoff, pollution, and the introduction of invasive species, such as zebra mussels (Cope et al. 2008). Mussels play an important role in their aquatic communities, such as providing habitat, filtering the water column, and depositing nutrients into the sediment. There is much scientific interest in what will happen to freshwater ecosystems as mussel species diversity and biomass declines.

The effect that mussels have on water filtration and waste recycling can vary widely based on the species, abundance, and environmental conditions present at the time. When water flow is low, such as in late summer, mussel communities can filter the entire volume. When water flow is high during times of melting and drainage, however, their effect is greatly reduced (Vaughn et al. 2004). Filtration performance is further affected by water temperature, with each species having its own optimal temperature. This means that in aquatic environments with multiple species of mussels, the ecosystem wide impacts of their filtration will vary widely based upon the relative dominance of each species, water flow, and temperature. Further complicating the equation is the fact that mussels also excrete ammonia, and their excretion rates can move in tandem with filtration rates, in the opposite direction, or not at all. It is all temperature dependent  (C.C. Vaughn 2010). The ammonia excreted by mussels plays an important role in lake and riverine ecosystems, boosting primary production and also benefiting consumers down the line (Spooner and Vaughn 2006). Even if excretion and filtration rates can be modeled for a set of known variables, it is important to remember that mussel communities can change in biomass and species dominance over time, and hydrological conditions are also dynamic.

Figure 3: This conceptual model demonstrates the complicated interplay between mussel species density, community structure, and ecosystem processes. (C.C. Vaughn 2010)

This example serves an important point. Attempting to understand how an aquatic environment will respond to changes in species composition is difficult. With so much uncertainty about the effects of biodiversity loss in North American freshwater ecosystems, we as a society have no idea what we may be getting ourselves in for. It is therefore prudent to prioritize the conservation of at-risk populations so that we do not have to contend with the damage that their losses may entail.

Works Cited

Dudgeon, David & Arthington, Angela & Gessner, Mark & Kawabata, Zen-Ichiro & Knowler, D & Lévêque, Christian & J Naiman, Robert & Prieur-Richard, Anne-Hélène & Soto, D & Stiassny, Melanie & A Sullivan, Caroline. (2006). Freshwater Biodiversity: Importance, Threats, Status and Conservation Challenges. Biological reviews of the Cambridge Philosophical Society. 81. 163-82. 10.1017/S1464793105006950.

Lundberg JG Kottelat M Smith GR Stiassny MLJ Gill AC. 2000. So many fishes, so little time: An overview of recent ichthyological discovery in continental waters. Annals of the Missouri Botanical Garden  87: 26–62.

Nelson JS Crossman EJ Espinosa-Pérez H Findley LT Gilbert CR Lea RN Williams JD. 2004. Common and Scientific Names of Fishes from the United States, Canada, and Mexico, 6th ed.

American Fisheries Society. Special Publication no. 29.

[IUCN] International Union for Conservation of Nature. 2011. IUCN Red List of Threatened Species, version 2011.2. IUCN. (13 June 2012; www.iucnredlist.org)

Freyhof J Brooks E. 2011. European Red List of Freshwater Fishes. Publications Office of the European Union.

Smith KG Darwall WRT eds. 2006. The Status and Distribution of Freshwater Fish Endemic to the Mediterranean Basin. International Union for the Conservation of Nature. (14 June 2012; http://data.iucn.org/dbtw-wpd/html/Red-medfish/cover.html)

Noel M. Burkhead, Extinction Rates in North American Freshwater Fishes, 1900–2010, BioScience, Volume 62, Issue 9, September 2012, Pages 798–808, https://doi.org/10.1525/bio.2012.62.9.5

Barnosky AD et al. .2011. Has the Earth’s sixth mass extinction already arrived? Nature 471: 51–57.

Cope WG et al.  2008. Differential exposure, duration, and sensitivity of unionoidean bivalve life stages to environmental contaminants. Journal of the North American Benthological Society 27: 451–462.

C.C. Vaughn. Biodiversity losses and ecosystem function in freshwaters: emerging conclusions and research directions. Bioscience, 60 (2010), pp. 25-35, 10.1525/bio.2010.60.1.7

Vaughn CC Gido KB Spooner DE. 2004. Ecosystem processes performed by unionid mussels in stream mesocosms: Species roles and effects of abundance. Hydrobiologia 527: 35–47.

Vaughn CC Spooner DE. 2006. Unionid mussels influence macroinvertebrate assemblage structure in streams. Journal of the North American Benthological Society  25: 691–70

Permeable Pavement Systems as a Mitigation Strategy to Combat Stormwater Outfall and Sea Level Rise

By Casey Dresbach, SRC intern

The EPA defines stormwater runoff as that which is generated from rain events that flow over land or impervious surfaces, such as paved streets, parking lots, and building rooftops, and does not soak into the ground (EPA, 2018). This accumulation of water ultimately ends up in coastal waters, but upon its journey it picks up a plethora of pollutants ranging from trash, chemicals, fecal matter, and sediment. These substances picked up by the runoff are compromising the health and water quality of these waters. A large portion of the global warming heat is accumulating in oceans worldwide. As a result, sea levels are rising through thermal expansion of water in the oceans and melting of ice sheets and glaciers on land.

Between 1998 and 2006 alone, tidal gauges showed sea levels in South Florida followed average global rate (0.04 to 0.20 inches per year) – but in 2006, local rates suddenly underwent a rapid acceleration, averaging about 0.20 inches to a half inch each year (Staletovich, 2016). Over the last decade, flood management has become increasingly important to several coastal states at risk such as Florida, Louisiana, New York, and California with each region varying in susceptibility to sea level rise. Flood management is commonly issued by drainage systems such as complex pipe networking. However, these projects are extremely costly and only seem to be dealing with the issue on a short-term basis. These stormwater controls are known as best management practices (BMPs) intended to filter out pollutants. Miami Beach has already undergone a major BMP using “gray stormwater infrastructure,” that is their $500 million drainage and water treatment system, one of which resides in a highly populated area (Harris, 2018). This coastal area, also known as Sunset Harbor Village, is home to local businesses, restaurants, bars, and boutique fitness enterprises. Yet, the effectiveness is not justifying the efforts taken to mitigate the impacts of sea level rise and urban development. The pump fails to filter out many of these pollutants pervading the streets and they ultimately end up into the coastal waters of Biscayne Bay (Figure 1).

Figure 1. Dirty Water Pumped Into Biscayne Bay (Caption: Dirty water pumped into Biscayne Bay in Miami Beach, FL. Snapshot from video taken by Miami Beach citizen.  (Lipscomb, 2019))

Benjamin O. Brattebo and Derek B. Booth conducted a study to examine the long-term stormwater quantity and quality performance of permeable pavement systems. Permeable pavement is made up of a matrix of concrete blocks or plastic structure with holes filled with sand, gravel or soil (Brattebo & Booth, 2003). The filling absorbs the outfall that might otherwise percolate into alternative places, most notably are coastal environments. The voids allow stormwater to seep through the pavement and into the soil. Asphalt pavement, an impervious system, was compared to four permeable pavements created in a monitored and controlled parking lot in Renton, Washington. Employees of King County Public Works facility utilize the parking facility during the workweek, Monday through Friday. Plastic Grasspave, plastic Gravelpace, concrete Turfstone, and concrete UNI Eco-stone were the permeable systems used. The first two plastic grids differed in their fill. The first was filled with sand and planted with grass and the second was filled with gravel only. Similarly, the first concrete was filled with soil and planted with grass while the latter was filled with gravel. Each permeable pavement had two parking stalls paired into one instrument station (Brattebo & Booth, 2003), which made up 8 stalls. The ninth stall was the asphalt-paved control. See Figure 2. During 15-minute rainfall events, runoff rates were cataloged. Water was collected and sampled in both the impermeable and permeable systems. Surface durability, infiltration capacity, and water-quality performance were assessed. Results showed that overall samples from permeable systems contained overwhelmingly lower levels of copper and zinc, and none had traces of diesel fuel or lead. Researchers indicated that while their findings support long-term success for infiltration via permeable systems, the success might not be universal in places with extremely arid or colder snow induced climates.

Figure 2. Plan View of 9 Parking Stalls JPEG aligned center. (Caption: 8 impermeable systems installed in parking lot alongside 1 control, the permeable asphalt concrete system. (Brattebo & Booth, 2003))

More research needs to be done in order to combat the challenges that arise with stormwater runoff and urban redevelopment continues on an upward trend. Long-term solutions and studies are crucial but as are short-term. A perfect balance of the two will help mitigate the detrimental impacts of pollutants trickling into larger water bodies that are utilized by the overall marine ecosystem, humans and coastal fauna included.

Works Cited

Brattebo, B. O., & Booth, D. B. (2003). Long-term stormwater quantity and quality performance of permeable pavement systems. Water Research , 37 (18), 4369-4376.

EPA. (2018, September 14). NPDES Stormwater Program. Retrieved from EPA: https://www.epa.gov/npdes/npdes-stormwater-program

Harris, A. (2018, April 18). Miami Beach’s future is ‘uncertain,’ experts say, but sea rise pumps are a good start. (Miami Herald) Retrieved March 20, 2019, from Miami Herald: Miami Beach’s future is ‘uncertain,’ experts say, but sea rise pumps are a good start: http://www.miamiherald.com/news/local/community/miami-dade/miami-beach/article209328849.html#storylink=cpy

Lipscomb, J. (2019). Videos Show Dirty Stormwater Pumped Into Biscayne Bay and Swallowed by Manatee. (M. N. Times, Producer) Retrieved from Miami New Times: https://www.miaminewtimes.com/news/videos-show-dirty-stormwater-pumped-into-biscayne-bay-and-swallowed-by-manatee-11068892

Staletovich, J. (2016, April 7). Miami Beach flooding spiked over last decade, UM study finds. (Miami Herald) Retrieved April 30, 2018, from Miami Herald: http://www.miamiherald.com/news/local/environment/article70145652.html

A microscopic organism with a macroscopic impact: How climate change is affecting harmful algal blooms and what this means for future generations

By Carolyn Hamman, SRC intern

Phytoplankton are photosynthetic microorganisms that exist in both marine and freshwater environments. There are several different types of phytoplankton each with their own unique preferred environmental parameters and strategies for growth. For example, some phytoplankton (called coccolithophores) use calcium to create protective plates they use as a defense mechanism (Beaufort et al. 2011). Phytoplankton are a vital component in aquatic ecosystems as they are responsible for the majority of primary productivity that occurs. In fact, phytoplankton have been considered a driver in climate as 30% of anthropogenic carbon emissions have been absorbed by the ocean and over 90% of the heat increase the Earth has seen the ocean has taken up (Hallegraeff 2010). While phytoplankton plays a vital role in many processes in the ocean, there are also occurrences of harmful algal blooms (HABs). HABs are phenomena that have been a natural process throughout history (Hallegraeff 2010). These blooms can be harmful for two reasons. Certain species of phytoplankton can produce different types of neurotoxins that have been known to cause different problems such as respiratory issues (such as with the Florida Red Tides) or gastrointestinal and neurological illnesses. HABs don’t have to necessarily produce toxins to be considered harmful. The dense covering that algal blooms can cause blocks UV light from reaching certain depths of the ocean. The high amount of phytoplankton will cause a depletion in nutrients that can disrupt other ecosystems who rely on the nutrients as well. Once the phytoplankton finally use up the nutrients, they die in massive amounts that deplete the oxygen in the water and causes massive anoxia (Hallegraeff 2010).

Climate refers to the large-scale changes that occur in the atmosphere, hydrosphere, and cryosphere (Hallegraeff 2010). There are natural fluctuations in the climate that have caused periods of warming or cooling. However, since around the Industrial Revolution, the CO2 levels have increased from 280 to >380 ppm, and there have been temperature increases in the past 40 years that are at a rate far faster than ever seen before (Hallegraeff 2010). Phytoplankton have short generation times and longevity, which means they can respond quickly to climate change. This is true for HABs as well. Though phytoplankton species can evolve and change, the changing environmental parameters will favor species with certain parameters. As climate continues to change, it is imperative to understand how HAB will respond. The issue is that there are numerous amounts of factors that all play a role in determining which species of algae bloom (Zingone & Enevoldsen 2000). These stressors caused by climate change can include increased temperature, enhanced surface stratification, alteration of ocean currents, intensification or weakening of nutrient upwelling, stimulation of photosynthesis by elevated CO2, reduced calcification from ocean acidification, and changes in land runoff and micronutrients (Hallegraeff 2010). Each of these parameters can be analyzed to determine how HAB will respond to climate change. In the past 30 years, there has been an increase in frequency and intensity of HAB as well as how widespread they are (Hallegraeff 2010).

As greenhouse gas concentrations have increased there has been an increase in surface temperature, lower pH, and changes in vertical mixing, upwelling, precipitation, and evaporation patterns (Moore et. al. 2008). As current strength and number of blooms have increased, the range of HAB has expanded (Hallegraeff 2010). Areas that had previously not seen HAB have noticed a significant increase in the past decade. HAB rely on temperature to bloom, and with an increase in overall temperature blooms have started to occur earlier than what has previously been observed (Hallegraeff 2010). Phytoplankton living in shallower areas will also be more effected by temperature than phytoplankton in open oceans (Hallegraeff 2010). This means that HAB closer to the shore will undergo larger changes than the populations in the open ocean. With increased greenhouse gases comes increase in sea-level, wind, and mixed-layer depth, which has an impact on the number of upwelling and downwelling events and thus concentrations of macronutrients (Hallegraeff 2010). The change in wind will also influence transport of nutrients by air (known as aeolian transport). The net result is a decrease in mixing depth at higher latitudes, which results in higher phytoplankton biomass (Hallegraeff 2010). A noticeable change in precipitation is occurring due to climate change as well, where there are now periods of concentrated rainfall followed by long dry spells. This change is causing certain dinoflagellates (a type of phytoplankton) to bloom in higher concentrations than previously seen before (Hallegraeff 2010).

A schematic showing how climate warming affects mixing in low and high latitudes. The differences in mixing results in differences in HAB (Hallegraeff 2010)

The environmental changes caused from climate change has caused HAB patterns not previously seen before. Going in to the future, the species-specific responses to these parameters can be used to better predict where HAB will occur and the concentration they could occur at. The potential issue with such predictions is that it is exceedingly difficult to be able to predict how several environmental parameters working together will cause phytoplankton to respond. It is recommended that there be a more improved global ocean observation system that can monitor all of these parameters simultaneously (Hallegraeff 2010). As previously mentioned, there could be increased adverse effects on human health due to increased HAB, but very little has been done to study how humans respond to different phytoplankton toxins (Moore et. al. 2008). More research is needed to evaluate associations between human health and HAB to better respond when harmful algal bloom occurrence continues to increase in to the future.

A graph showing the relationship between the number of algal blooms and human population over time. Populations and boom frequency have both increased over time (Zingone & Enevoldsen 2000)

Works cited

Beaufort, L., Probert, I., De Garidel-Thoron, T., Bendif, E. M., Ruiz-Pino, D., Metzl, N., … & Rost, B. (2011). Sensitivity of coccolithophores to carbonate chemistry and ocean acidification. Nature476(7358), 80.

Hallegraeff, G. M. (2010). Ocean Climate Change, Phytoplankton Community Responses, And Harmful Algal Blooms: A Formidable Predictive Challenge. Journal of Phycology, 46(2), 220-235. doi:10.1111/j.1529-8817.2010.00815.x

Moore, S. K., Trainer, V. L., Mantua, N. J., Parker, M. S., Laws, E. A., Backer, L. C., & Fleming, L. E. (2008). Impacts of climate variability and future climate change on harmful algal blooms and human health. Environmental Health, 7(S4), 1-12. doi:10.1186/1476-069x-7-s2-s4

Zingone, A., & Enevoldsen, H. O. (2000). The diversity of harmful algal blooms: A challenge for science and management. Ocean & Coastal Management, 43(8-9), 725-748. doi:10.1016/s0964-5691(00)00056-9

A Summary of Acoustic Tagging and Juvenile Salmon Acoustic Telemetry System Program in the Northwestern United States

By Brenna Bales, SRC intern

Before the existence of satellite and acoustic tracking technologies, the most we knew about a certain marine species’ range was from either visual observations or catch data. By developing these systems and scientists cooperating globally by sharing their data, we have learned that some “tropical” species like tiger sharks are not tropical at all but can in fact go as far north as Maine or Canada and out thousands of miles into the mid-Atlantic on a single migration from Florida (sharktagging.com). In 1999, an estimated 11,800 electronic tags (both satellite and acoustic) were placed on marine mammals, fish, invertebrates, reptiles, and birds around the world (Stone et al, 1999). There is a major difference between these two technologies, however. While satellite tags will track an animal wherever it goes as long as it can communicate with a satellite (meaning the tag must hit the surface to be detected), acoustic tags (Image 1) must be within range to an underwater hydrophone for the signal to be detected. This enables acoustically tagged animals to be tracked on a much finer scale without the need for the animal to come to the surface.

Image 1: Differently sized acoustic tags that would be used internally to monitor movements of animals.

A research organization may set up a hydrophone array over a certain area to pinpoint their tagged animals’ locations; however, this array may also detect other animals that have been acoustically tagged by different research organizations. This can be helpful to everyone, as only one hydrophone is needed to track all kinds of animals and their tags, such as sawfish, sharks, and marine mammals; however, private interests may hinder this (Grotheus 2009). Lastly, acoustic tagging has benefits in that it can be used to track multiple individuals within a population in one location versus a small number of animals tracked over different time scales and locations (Huepel et al, 2006).

In 2001, the U.S. Army Corps of Engineers Portland District decided that they wanted to track juvenile salmon in the Columbia river basin through their migration to the Pacific Ocean. There were several goals to the JSATS (Juvenile Salmon Acoustic Telemetry System) project, including 1) assessment of survival and habitat use of juvenile salmonids migrating through the estuarine environment 2) estimation of route-specific dam passage survival of juvenile salmonids 3) determination of fish survival and migration behavior, and 4) to determine effects of water temperature stratification and dissolved gas (https://waterpower.pnnl.gov/jsats/). By 2008, 4,140 JSATS  and 48,433 passive integrated transponder (PIT)- tagged yearling Chinook salmon (Oncorhynchus tshawytscha) had been tagged (McMichael et al, 2010). The dams are shown in Image 2 along with the route that the salmon migrated towards the Pacific Ocean.

Image 2: Study area used in JSATS in the Snake and Columbia river basins in 2008. Red circles demarcate the hydrophone array locations and the star marks the release location of the tagged yearling Chinook salmon.

The researchers on the project concluded that the JSATS tags gave more survival location data with higher precision than the PIT tags (McMichael et al, 2010). The JSATS tags also transmitted every 5 seconds, which is optimal for the current study in tracking such small-scale movements around the local dams. All components of the system were non-proprietary, unlike many other arrays currently established. A major outcome from this was the competitive nature in which the U.S. Army Corps of Engineers bid for reductions in sizing and pricing for these tags, leading to many advances in the technology. The study is on-going, and research is being conducted on the biological effects of tagging and how the environment is affecting the receivers and their detection capability. This telemetry system has been designed extremely efficiently and should be used as a model for other up and coming acoustic tagging endeavors.

Literature Cited

Grothues, T.M., 2009. A review of acoustic telemetry technology and a perspective on its diversification relative to coastal tracking arrays. In Tagging and tracking of marine animals with electronic devices (pp. 77-90). Springer, Dordrecht.

Heupel, M.R., Semmens, J.M. and Hobday, A.J., 2006. Automated acoustic tracking of aquatic animals: scales, design and deployment of listening station arrays. Marine and Freshwater Research, 57(1), pp.1-13.

McMichael, G.A., Eppard, M.B., Carlson, T.J., Carter, J.A., Ebberts, B.D., Brown, R.S., Weiland, M., Ploskey, G.R., Harnish, R.A. and Deng, Z.D., 2010. The juvenile salmon acoustic telemetry system: a new tool. Fisheries, 35(1), pp.9-22.

Stone, G., Schubel, J. and Tausig, H., 1999. Electronic marine animal tagging: New frontier in ocean science. OCEANOGRAPHY-WASHINGTON DC-OCEANOGRAPHY SOCIETY-, 12, pp.24-27.

Image 1 source: https://commons.wikimedia.org/wiki/File:Example_of_Acoustic_Telemetry_Tags_for_Fisheries_Research.jpg

Image 2: McMichael, G.A., Eppard, M.B., Carlson, T.J., Carter, J.A., Ebberts, B.D., Brown, R.S., Weiland, M., Ploskey, G.R., Harnish, R.A. and Deng, Z.D., 2010. The juvenile salmon acoustic telemetry system: a new tool. Fisheries, 35(1), pp.9-22.

Migration Dynamic of Juvenile Southern Bluefin Tuna

By: Julia Saltzman, SRC Intern

Large-scale migrations are crucial to many different marine species. In southern bluefin tuna, this life history trait is critical for sustaining their valuable fisheries, and as such there are many scientific research programs designed to monitor the management of the species. Telemetry technology (remote tracking of spatial locations and movements) has made cycles more generally observable, however quantifying variability and plasticity of migration schedules still remains a challenge. In this study from Patterson et al. (2018), movements from 110 individual juvenile southern bluefin tuna were estimated from the period of 1998-2011. The authors found that individuals demonstrated considerable variability in migratory patterns between the years. Patterns observed that juvenile southern bluefin tuna progressively spent less time in shelf waters, and the moved east, rather than west into the Tasman Sea for a higher period then heading west into the India Ocean. In addition, it was found that the further southern bluefin tuna move from the Great Australian Bight (GAB), the more time they spend migrating. This study also determined three areas associated with the residency of juvenile southern bluefin tuna. These areas of residence were far different from the known areas of residence in the past. The productivity in these residency regions displayed a seasonal cycle.

This study asserted that much like other large marine animals who use temperate latitudes, juvenile southern bluefin tuna also undertake long distance and large-scale migrations. In addition, while fish were observed to migrate to key areas, their patterns, especially in the winter months, varied both on an individual and yearly basis. Researchers suggested that for fast growing, immature, large, predators, such as those studied here their migration may be related to environmentally availability, rather than cues which are fixed such as day length. Other environmental factors also impact the migrations; for example, because the fish is a visual predator, they prefer to hunt in clear waters away from areas of high turbidity and high primary productivity. In addition, it is likely that seasonal populations of small pelagic fish in the GAB coincide with the migration of the southern bluefin tuna.

Through the use of tag deployment and geolocation of juvenile southern bluefin tuna, and Hidden Markov Models to estimate when individuals were migrating, important insights were obtained on the individuals within the same period and within individuals across multiple years. The complexity of migration routes appears to be related to sea surface temperature, productivity, and the physiology of the individual southern bluefin tuna. This report provides scientists and fisheries managers with the information to effectively manage southern bluefin tuna. This species, which has faced massive declines in the past due to poor management strategies, is now much better managed due to an understanding of their varying migratory patterns, especially those of juveniles.

Work Cited:

Patterson, T. A., Eveson, J. P., Hartog, J. R., Evans, K., Cooper, S., Lansdell, M., … & Davies, C. R. (2018). Migration dynamics of juvenile southern bluefin tuna. Scientific reports8(1), 14553.