SOUTH BAY RESEARCH NOTES & RESOURCES:
"Boston Harbor is approximately 44 square miles in area. It has salinity features controlled chiefly by tides and is a vertically mixed estuary having more affinities with embayments than estuaries and aquatic life that is marine rather than estuarine.
Discharges of municipal and industrial wastes originating in the Boston metropolitan and harbor areas caused degraded water in all of Boston Harbor and associated bays inland from the harbor mouth near Massachusetts Bay. A paucity in the variety of aquatic life in these waters showed such degradation.
Deposition of nutrients from these wastes effected overly-abundant, pollution-indicating populations of polychaete worms that exceeded 200 per square foot in 34 square miles (80 percent) of Boston Harbor. About 14 square miles (30 percent) of Boston Harbor were grossly polluted as was suggested by polychaete worms that numbered 1,000 or more per square foot. Oily residues, foul odors, and suspended sewage-like particles often were apparent in most reaches of the harbor.
Biological Aspects of Water Quality Charles River and Boston Harbor, Massachusetts, July-August 1967, United States Department of the Interior, Federal Water Pollution Control Administration (1968).
Discharges of municipal and industrial wastes originating in the Boston metropolitan and harbor areas caused degraded water in all of Boston Harbor and associated bays inland from the harbor mouth near Massachusetts Bay. A paucity in the variety of aquatic life in these waters showed such degradation.
Deposition of nutrients from these wastes effected overly-abundant, pollution-indicating populations of polychaete worms that exceeded 200 per square foot in 34 square miles (80 percent) of Boston Harbor. About 14 square miles (30 percent) of Boston Harbor were grossly polluted as was suggested by polychaete worms that numbered 1,000 or more per square foot. Oily residues, foul odors, and suspended sewage-like particles often were apparent in most reaches of the harbor.
Biological Aspects of Water Quality Charles River and Boston Harbor, Massachusetts, July-August 1967, United States Department of the Interior, Federal Water Pollution Control Administration (1968).
Indicator species & Ecological Degradation
Dominance of Tolerant &/or Opportunistic Biota:
The presence of macroscopic Beggiatoa mats within the 2000ft radius are an indicator of high sulfide levels resulting from the buried, decomposing sewage. Filamentous sulfur bacteria (Beggiatoa) fall into this category as Chemolithotrophic organisms that thrive in the oxicanoxic interface.
Polycheates in residential buildings. High abundance and dominance of polychaete worms (e.g., Capitella species) in the sediment. A community dominated by a few opportunistic species is a classic indicator of high organic enrichment.
Indicator Species (Bioindicators):
The presence of certain sulfur-cycling bacteria indicates high organic loading, while the absence of sensitive macroinvertebrates confirms poor biological integrity.
Beggiatoa thrives at oxic-anoxic interfaces. This area has become sulfur-rich due to the pollution, enabling organisms to create chemolithotrophic mats. The current presence of Beggiatoa mats is an indicator of environmental deterioration andhigh sulfide levels resulting from sewage dumping and organic runoff.
High levels of Fecal Indicator Bacteria (FIB) in the water column (e.g., E. coli, Coliforms), indicating ongoing public health risks and sewage presence.
Sensitive, Native, &/or Specialist Biota:
Total absence of sensitive species expected in the Reference Condition, such as varied fish, shellfish, and sensitive macroinvertebrates. The absence of tidal flat or salt marsh plants and animals that would normally colonize these banks if they were unpolluted. These species are missing as they cannot tolerate the altered conditions.
The site exhibits significant Ecological Degradation and Impairment based on the biological evidence. The impact of the active CSO and legacy pipes continue to act as point and non-point sources of contamination, preventing natural recovery. The persistence of the Beggiatoa mats and high E. coli counts to the need for remediation, as natural recovery cannot occur until the source of organic enrichment is removed.
There is a continuing presence of FIB and specific bacteria that thrive in highly contaminated freshwater/estuarine inputs. There are specific microbial mats and unique bacterial communities present at the outflow points. There is an absence of clean-water aquatic life (e.g., clean-water fish, amphibian larvae).
The presence of macroscopic Beggiatoa mats within the 2000ft radius are an indicator of high sulfide levels resulting from the buried, decomposing sewage. Filamentous sulfur bacteria (Beggiatoa) fall into this category as Chemolithotrophic organisms that thrive in the oxicanoxic interface.
Polycheates in residential buildings. High abundance and dominance of polychaete worms (e.g., Capitella species) in the sediment. A community dominated by a few opportunistic species is a classic indicator of high organic enrichment.
Indicator Species (Bioindicators):
The presence of certain sulfur-cycling bacteria indicates high organic loading, while the absence of sensitive macroinvertebrates confirms poor biological integrity.
Beggiatoa thrives at oxic-anoxic interfaces. This area has become sulfur-rich due to the pollution, enabling organisms to create chemolithotrophic mats. The current presence of Beggiatoa mats is an indicator of environmental deterioration andhigh sulfide levels resulting from sewage dumping and organic runoff.
High levels of Fecal Indicator Bacteria (FIB) in the water column (e.g., E. coli, Coliforms), indicating ongoing public health risks and sewage presence.
Sensitive, Native, &/or Specialist Biota:
Total absence of sensitive species expected in the Reference Condition, such as varied fish, shellfish, and sensitive macroinvertebrates. The absence of tidal flat or salt marsh plants and animals that would normally colonize these banks if they were unpolluted. These species are missing as they cannot tolerate the altered conditions.
The site exhibits significant Ecological Degradation and Impairment based on the biological evidence. The impact of the active CSO and legacy pipes continue to act as point and non-point sources of contamination, preventing natural recovery. The persistence of the Beggiatoa mats and high E. coli counts to the need for remediation, as natural recovery cannot occur until the source of organic enrichment is removed.
There is a continuing presence of FIB and specific bacteria that thrive in highly contaminated freshwater/estuarine inputs. There are specific microbial mats and unique bacterial communities present at the outflow points. There is an absence of clean-water aquatic life (e.g., clean-water fish, amphibian larvae).
biota around Prior canal & South Bay
Fauna & Wildlife:
Common Raccoon (Procyon lotor), iNaturalist Observation No. 35097043, Oct 30 2019, Summer St., Boston, MA, USA
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Jassa, iNaturalist Observation No. 245291464, Oct 2 2024, out of water and crawling around on D Street / W Broadway, Boston, MA, USA
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Insects:
Greenhouse Millipede (Oxidus gracilis), iNaturalist Observation No. 298977129, Jul 18, 2025, Fort Point, Boston, MA, USA
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Brilliant Jumping Spider (Phidippus clarus), iNaturalist Observation No. 295534138, July 2025, Fort Point, Boston, MA, USA
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Swamp Darner Epiaeschna heros), iNaturalist Observation No. 224076248, Jun 20, 2024, Fort Point, Boston, MA, USA
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Nessus Sphinx (Amphion floridensis), iNaturalist Observation No. 297436194, July 12, 2025, South End, Boston, MA, USA
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Crane Fly, iNaturalist Observation No. 154735644, April 13, 2025, Fort Point & Congress St, Boston, MA, USA
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Chinese Mantis (Tenodera sinensis), iNaturalist Observation No. 133122869, Aug 31, 2022, Fort Point & Congress St, Boston, MA, USA
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Crane Fly, iNaturalist Observation No. 134969569, Sept 14, 2022, S Station Connector, Boston, MA, USA
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Flora:
Dodders (Cuscuta), iNaturalist Observation No. 308004075, Aug 21, 2025, Fort Point, Boston, MA, USA
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Bladder Wrack (Fucus vesiculosus), iNaturalist Observation No. 285458718, May 30, 2025, Pier 4, Boston, MA, USA
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Moss & Lichen
Sunburst Lichens (Xanthoria), iNaturalist Observation No. 237079460, Aug 19, 2024, Fort Point, D Street / West Broadway, Boston, MA, USA
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Rock Greenshield Lichen (Flavoparmelia baltimorensis), iNaturalist Observation No. 51257333, July 28, 2020, Fort Point, Harbor Trail, Boston, MA.
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Star Rosette Lichen (Physcia stellaris), iNaturalist Observation No. 172033173, July 8, 2023, Summer St, Harbor Trail, Boston, MA, USA
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Candleflame Lichen (Candelaria concolor), iNaturalist Observation No. 146665960, Jan. 13, 2023, Union Park St. Playground, Boston, MA, USA
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Golden Moonglow Lichen Dimelaena oreina), iNaturalist Observation No. 290848164, Aug 4, 2024, Fort Point, Harbor Trail, Boston, MA, USA
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Common Greenshield Lichen (Flavoparmelia caperata), iNaturalist Observation No. 99459596, Oct. 25, 2021, Kneeland & Harrison, Boston, MA, USA
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Mealy Rim-Lichen (Lecanora strobilina), iNaturalist Observation No. 245145887, Oct 1, 2024, Fort Point, D Street / West Broadway, Boston, MA, USA
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Fungi, Smut, & Slime Mold
Yellow Gymnopilus (Gymnopilus luteus), iNaturalist Observation No. 317582720, Sep 29, 2025, Fort Point, Boston, MA, USA
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Green-spored Parasol (Chlorophyllum molybdites), iNaturalist Observation No. 237079700, Fort Point, Aug 19, 2024
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Dryad's Saddle (Cerioporus squamosus), iNaturalist Observation No. 288622874, May 26, 2025, Fort Point Channel, Boston, MA, US
Wolfs Milk Genus Lycogala), iNaturalist Observation No. 20735164, South End, near Castle Sq. Park, Feb 24 2019,
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Slime Mold (Fuligo septica), iNaturalist Observation No. 299070075, Jul 15, 2025,
Fort Point, Boston, MA, USA
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Slime Mold (Fuligo septica), iNaturalist Observation No. 302061781, Jul 29, 2025,
South Boston Waterfront, Boston, MA, USA
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Trooping Crumble Cap (Coprinellus disseminatus), iNaturalist Observation No. 306092644, Fort Point Harborwalk, Martin's Park between Silverline & Congress St, Aug 13, 2025.
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Trooping Crumble Cap (Coprinellus disseminatus), iNaturalist Observation No. 171840785, Fort Point Harborwalk, Martin's Park between Silverline & Congress St, July 18 2025.
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False Turkeytail (Stereum lobatum), iNaturalist Observation No. 192253223, Long Wharf, Nov26 2023.
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Black-staining Polypore (Meripilus sumstinei), iNaturalist Observation No. 91337376, Seaport Blvd, Aug 15 2021
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Bark Mycena (Mycena corticola), iNaturalist Observation No. 99553270, Harrison Ave & Kneeland St, Oct 27, 2021.
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Ganoderma sessile, iNaturalist Observation No. 231822602, -July 26, 2024, Biomedical Research and Public Health Building, Boston, MA
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Other
Cyathus, iNaturalist Observation No. 302062553, Jul 29, 2025, Fort Point, Boston, MA, USA
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Cyathus, iNaturalist Observation No. 302062553, Jul 29, 2025, Fort Point, Boston, MA, USA
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Earthstars Genus Geastrum, iNaturalist Observation No. 92370962, Aug 24, 2021,
Rose Fitzgerald Kennedy Greenway, MA, USA
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Earthstars Genus Geastrum, iNaturalist Observation No. 90263261, Aug 24, 2021, Dewey Square Park, Boston, MA
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*See more on Phallomycetidae and Nidulariaceae genetic research:
- Gjøvik, Ashley M. “The Pseudocolus Stinkhorn and the Survival of Ediacaran Architecture: A Genomic & Structural Reassessment of a Misclassified Proto-Animal”. The Journal of Decolonized Ecology and Evolution 1, no. 1 (June 16, 2025). https://doi.org/10.5281/zenodo.15675088.
- Gjøvik, Ashley M. High-confidence Genetic Alignment Between Sphaerobolus (the “Cannonball” Fungi) & Turritopsis (the “Immortal Jellyfish“). The Journal of Decolonized Ecology and Evolution 1, no. 1 (June 11, 2025). https://doi.org/10.5281/zenodo.15639701.
Microbiota (Bacteria, Archaea, Diatoms):
Viruses & Parasites:
Pokeweed Mosaic Virus (Potyvirus phytolaccae), iNaturalist Observation No. 308162777, Aug 21, 2025, Fort Point, Boston, MA, USA
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Poison Ivy Leaf Mite (Aculops rhois), iNaturalist Observation No. 145230425, Nov. 6 2022, Fort Point Boston
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Poison Ivy Leaf Mite (Aculops rhois), iNaturalist Observation No. 145231146, Nov. 7 2022, Fort Point Boston
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Tubakia suttoniana, iNaturalist Observation No. 323009234, Oct. 25 2025, Washington St at Union Pk, Boston
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Quince Rust (Gymnosporangium clavipes), iNaturalist Observation No. 169948571, South Boston, D St near South Boston Maritime Park, June 28 2023.
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Pear Rust (Gymnosporangium sabinae), iNaturalist Observation No. 59569039, Harrison Ave, South End, Sept. 14 2020.
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Complex Coleosporium solidaginis, iNaturalist Observation No. 246717121, Fort Point, Oct. 10 2024.
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Horned Oak Gall Wasp (Callirhytis quercuscorniger), iNaturalist Observation No. 11510449, E India Row, Aug 27 2018
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2025 Field Study
All photos captured by Ashley Gjovik based on samples obtained in her South End basement apartment.
MICROSCOPIC IMAGES WITH POSSIBLE IDENTIFICATION:
Feb 11, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: sulfur oxidizing bacteria i.e., Thioploca
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April 19 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: cyanobacteria, i.e., Oscillatoriaceae
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April 19 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: cyanobacteria, i.e., Oscillatoriaceae
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April 7 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: Oscillatoria lutea
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Feb. 14 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: sulfur oxidizing bacteria i.e. Thiolava (Tagoro underwater volcano, 2017)
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Feb 5 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: Capitella capitata complex (Annelida, Capitellidae)
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Feb. 11, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: sulfur oxidizing bacteria i.e., Thioploca
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May 20, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: sulfur oxidizing bacteria i.e. Thiolava
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Feb. 14 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: iron oxidizing bacteria (Chemolithotrophic microbial mats in an open pond in the continental subsurface – implications for microbial biosignatures, January 2014).
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April 7 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: sulfur oxidizing bacteria, i.e., Beggiatoa
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Feb. 1, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: cyanobacteria, i.e., Oscillatoria
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Feb. 13, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: iron oxidizing bacteria (FeOB) i.e., Mariprofundus ferrooxydans
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Feb 13 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Pterospermopsimorpha?
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Feb. 13 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: iron oxidizing bacteria (FeOB) i.e., Mariprofundus ferrooxydans
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Feb. 9 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: sulfur oxidizing bacteria
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Feb. 11 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Possible identification: iron oxidizing bacteria (FeOB)
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Photos on the left side taken by Ashley Gjovik.
Feb 26, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Volyn biota?
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Feb 5, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Chancelloria sp.?
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Photos on the left side taken by Ashley Gjovik.
2025 FIELD STUDY: UNIDENTIFIED SPECIMENS
Jan 17, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 1 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 1 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 9 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 13, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Jan 17 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 2 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 17 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Jan. 18 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb 11, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb 2, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 6, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb 14, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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April 19 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 14 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 14 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 13 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 14 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Jan 23 2026 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Jan 26 2026 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Jan 12 2026 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 16 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb 04 2026 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb 02 2026 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 11 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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April 17 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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April 7 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Jan. 2 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Jan. 2 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 14 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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April 26 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 14 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 14 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 9 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 11 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 14 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb. 2 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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April 7, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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Feb 2, 2025 | microscopy (AmScope) sample obtained in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs.
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All photos take by Ashley Gjovik.
MACROSCOPIC IMAGES WITH POSSIBLE IDENTIFICATION:
1) FIELDSTONE (PUDDINGSTONE) ERODED FROM WITHIN THE VOID OF A DOUBLE-PARTY WALL ATOP BLUE CLAY AND PRIOR MARSH/PEAT
Nov 22 2025 | hole & surrounding growths found in fieldstone of South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
Nov 22 2025 | hole & surrounding growths found in fieldstone of South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
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Nov 22 2025 | hole & surrounding growths found in fieldstone of South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
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2) LED MICROSCOPE
LED Microscope (50-1000x): sample from basement apartment
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LED Microscope (50-1000x): sample from basement apartment
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LED Microscope (50-1000x): sample from basement apartment
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LED Microscope (50-1000x): sample from basement apartment
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LED Microscope (50-1000x): sample from basement apartment; What is this?!
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LED Microscope (50-1000x): sample from basement apartment
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3) FIELDSTONE EXTERIOR WALL
Feb. 2 2025 | growths found on exterior facing (underground) fieldstone in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
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Feb. 15 2025 | growths found on exterior facing (underground) fieldstone in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
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Feb. 2 2025 | growths found on exterior facing (underground) fieldstone in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
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Feb. 2 2025 | growths found on exterior facing (underground) fieldstone in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
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4) GROWTHS AROUND THE KITCHEN
Jan. 27 2025 | "dust" found on center of paper towel rack next to kitchen sink in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
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Jan. 27 2025 | "carpet" next to stone kitchen floor starts to grow in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
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5) CULTURES & ASSAYS:
Jan. 27 2025 | in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
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Jan. 27 2025 | in South End basement ~1,200 ft / 365 m from Canal for 160+ yrs
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All photos taken by Ashley Gjovik.
Examples of Zetaproteobacteria & Gammaproteobacteria habitats:
Photographs of Zetaproteobacteria habitats. (A-D) Marine hydrothermal vent mats, where Zetaproteobacteria have been found in highest abundance. (A) Curdtype and (B) veil-type Fe mats, from Loihi Seamount. (C) Mn-crusted Fe mat from the Ula Nui site, Loihi. Fe mat visible under broken surface (bottom right). (D) Fe mats on the Golden Horn Chimney, at the Urashima vent site, Mariana Trough. Mcallister, Sean & Moore, Ryan & Gartman, Amy & Luther, George & Emerson, David & Chan, Clara. (2019). The Fe(II)-oxidizing Zetaproteobacteria: historical, ecological and genomic perspectives. FEMS Microbiology Ecology. 95. 10.1093/femsec/fiz015.
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Thiothrix bacteria at Sulphur Spring. Thiothrix spp. are sessile filamentous ‘sulfur bacteria’. They thrive naturally in masses in the hydrogen sulphide-rich outflow waters of sulphur springs where they form dense floating tufts that adhere to almost any surface. Strauss, Harald & Chmiel, Hannah & Christ, Andreas & Fugmann, Artur & Hanselmann, Kurt & Kappler, Andreas & Königer, Paul & Lutter, Andreas & Siedenberg, Katharina & Teichert, Barbara. (2015). Multiple sulphur and oxygen isotopes reveal microbial sulphur cycling in spring waters in the Lower Engadin, Switzerland. Isotopes in environmental and health studies. 52. 1-19. 10.1080/10256016.2015.1032961.
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View of the surface of a rust-colored nodule from galvanized iron pipe showing flocculent-type precipitate and Gallionella microcolonies. Ridgway, Harry & Means, E & Olson, Betty. (1981). Iron Bacteria in Drinking-Water Distribution Systems: Elemental Analysis of Gallionella Stalks, Using X-Ray Energy-Dispersive Microanalysis. Applied and environmental microbiology. 41. 288-97. 10.1128/AEM.41.1.288-297.1981.
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(A) SEM micrograph of the 2 months old microbial mat from the flow reactor at site 1327B, showing the twisted EPS-stalks of Gallionella sp. and/or Mariprofundus sp. (B) Detail of young EPS-stalks sampled after 2 months, still showing a pristine filamentous structure. Heim, Christine & Ionescu, Danny & Reimer, Andreas & de Beer, Dirk & Quéric, Nadia-Valérie & Reitner, Joachim & Thiel, Volker. (2015). Assessing the utility of trace and rare earth elements as biosignatures in microbial iron oxyhydroxides. Frontiers in Earth Science. 3. 10.3389/feart.2015.00006.
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In situ close-up video still photo of an orange Beggiatoaceae mat in Guaymas Basin, taken by the bottom-facing Alvin camera a few centimeters above the seafloor during Alvin dive 4872 in the Cathedral Hill area of Guaymas Basin (27°N00.70/111°W24.25). Buckley, Andrew & MacGregor, Barbara & Teske, Andreas. (2019). Identification, Expression and Activity of Candidate Nitrite Reductases From Orange Beggiatoaceae, Guaymas Basin. Frontiers in Microbiology. 10. 10.3389/fmicb.2019.00644.
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Photographs of the Beggiatoa mat. Underwater picture of patches of white mat on the mangrove sediment. Jean, Maïtena R N et al. “Two new Beggiatoa species inhabiting marine mangrove sediments in the Caribbean.” PloS one vol. 10,2 e0117832. 17 Feb. 2015, doi:10.1371/journal.pone.0117832
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Biota in fort point benthic & Pelagic zones
Fauna: Fish
Striped Bass (Morone saxatilis), iNaturalist Observation, 56457923, Aug 14, 2020, Long Wharf, Waterfront, Boston, MA.
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Cunner (Tautogolabrus adspersus), iNaturalist Observation, 319653502, Sept. 30, 2025, D Street / West Broadway, Boston, MA.
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Ray-finned Fishes (Menidia?), iNaturalist Observation, 309822557, Aug 27, 2025,
Fort Point, Boston, MA, USA
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Ray-finned Fishes (Menidia?), iNaturalist Observation, 309822557, Aug 27, 2025,
Fort Point, Boston, MA, USA
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Fauna: Arthropoda
Caprella, iNaturalist Observation No. 245316688, Oct 2, 2024, Fort Point,
Boston, MA, USA
Japanese Skeleton Shrimp (Caprella mutica), iNaturalist Observation No. 245665188, Aug 3, 2024, Fort Point.
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Japanese Skeleton Shrimp (Caprella mutica), iNaturalist Observation No. 309823806, D Street, Aug 27, 2025.
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Annelida, Polychaeta
Spaghetti Worms (Terebellidae), iNaturalist Observation No. 14511714, July 18 2018, 1 Central Wharf, Boston, MA
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Fauna: Gastropod
Bushy-backed Nudibranch (Dendronotus frondosus), iNaturalist Observation No. 282358173, May 17 2025, South Boston Waterfront, Boston, MA
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Fauna: Cnidarians
- Aurelia blooms
- Aurelia blooms
Moon Jelly (Aurelia aurita), iNaturalist Observation No. 302928685, Aug 1 2025, Fort Point, Boston, MA
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Moon Jelly (Aurelia aurita), iNaturalist Observation No. 295226618, July 3 2025, Fort Point, Boston, MA
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Moon Jelly (Aurelia aurita), iNaturalist Observation No. 285108267, May 29 2025, Fort Point, Boston, MA
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Moon Jelly (Aurelia aurita), iNaturalist Observation No. 295226618, July 3 2025, Fort Point, Boston, MA
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Lion's Mane Jelly (Cyanea), iNaturalist Observation No. 281076794, Aug. 14 2025, South Boston, MA
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Lion's Mane Jelly (Cyanea), iNaturalist Observation No. 281076794, Aug. 14 2025, South Boston, MA
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Fauna: Tunicates
Chain Tunicate (Botrylloides violaceus), iNaturalist, Observation No. 309874602, Aug 27, 2025, Fort Point, D Street / West Broadway, Boston, MA, USA
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Chain Tunicate (Botrylloides violaceus), iNaturalist, Observation No. 245145414, Oct 1, 2024, Fort Point, Boston, MA
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Star Tunicate Botryllus schlosseri), iNaturalist Observation No. 245262948, Oct 2, 2024, Fort Point, D Street / West Broadway, Boston, MA, USA
Sea Vase (Ciona intestinalis), iNaturalist Observation No. 311370100, Sep 3, 2025, Fort Point, D Street / West Broadway, Boston, MA, USA
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Sea Vase (Ciona intestinalis), iNaturalist Observation No. 309822626, Aug 27, 2025,
D Street / West Broadway, Boston, MA, USA
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Sea Vase (Ciona intestinalis), iNaturalist Observation No. 317696629, Sep 21, 2025, Fort Point, Boston, MA, USA
Fauna: Porifera
Halichondria, iNaturalist, Observation 309822459, Aug 27, 2025, Fort Point, D Street / West Broadway, Boston, MA, USA
Flora & Macroalgae:
none/unknown
none/unknown
iNaturalist, Observation No. 245148246, Oct 1, 2024, Fort Point, D Street / West Broadway, Boston, MA, USA
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iNaturalist, Observation No. 245148246, Oct 1, 2024, Fort Point, D Street / West Broadway, Boston, MA, USA
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Sugar Kelp (Saccharina latissima), iNaturalist Observation No. 276680657, Apr 29, 2025, South Boston Harbor Walk near Fan Pier, Boston, MA, USA
Knotted Wrack (Ascophyllum nodosum), iNaturalist Observation No. Apr 4, 2025, Fort Point, D Street / West Broadway, Boston, MA, USA
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Broadleaf Sea Lettuce (Ulva lactuca), iNaturalist Observation No. 166067594, June 7 2023, Fan Pier / Seaport, Boston, MA, USA
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Rockweed (Fucus distichus), iNaturalist Observation No. 294910588, July 3 2025, Long Wharf, Boston, MA, USA
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Phytoplankton & Microeukaryotes:
Fragilaria, iNaturalist Observation No. 162777596, May 20 2023, Seaport, Boston, MA, USA
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Achnanthes, iNaturalist Observation No. 166175932, June 6 2023, Seaport, Boston, MA, USA
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Unexpected Bryozoan (Tricellaria inopinata), iNaturalist Observation No. 34416223, Oct 15 2019, Central Wharf Boston, MA, USA
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Prokaryotic Communities:
"In Fort Point Channel, about one-quarter of an inch of rain would, on average, raise the fecal coliform count above the 200 colonies/100 ml water quality standard, while at the mouth of the inner harbor, near the airport, it would, on average, take more than two inches of rain before fecal coliform counts would exceed standards."
Combined Sewer Overflow Receiving Water Monitoring Boston Harbor and Its Tributary Rivers October 1990-September 1991 (January 1993).
"The South Station site and immediate area are located on filled tidelands, initially built beginning in the early part of the 19th century with the construction of wharves and piers along the western shoreline of Fort Point Channel. Boston Inner Harbor is included on the 2012 Final Integrated List of Waters as Category 5 and impaired for polychlorinated biphenyls (PCBs) in fish tissue, fecal coliform, enterococcus, dissolved oxygen, and other impairments, and requires one or more TMDL."
South Station Expansion, Draft Environmental Impact Report: Chapter 4 – Potential Environmental Impacts and Mitigation, Massachusetts Department of Transportation (October 2014).
"Stations 018, 019, 075, 138 and 178-Fort Point Channel. Although Fort Point Channel is not used for swimming, high bacterial counts are a concern and were measured frequently. Of the 105 samples collected, 26 were higher than 104/100 ml. At Station 075 near the BOS 070 outfall, 15 out of the 19 samples were above 104/ 100 ml. Water quality improved as the sample locations moved further away. Station 018 recorded 6 out of 20 samples with elevated bacterial levels. None of the samples in Inner Harbor Stations 019 and 138 exceeded standards. The MWRA added Station 075 near the BOS 070 outfall and Station 178 at the Moakley Bridge in 2009 to provide data along the length of the channel. Several CSOs can discharge into this area, BOS 064, BOS 065, BOS 068, BOS 070, and BOS 073. The most active is BOS 070 which discharges flows from the MWRA's CSO Facility at Union Park Pumping Station. It should be noted that Union Park Pumping Station discharges are screened and disinfected prior to discharge into the Roxbury Canal Conduit. A plot of Enterococcus bacteria counts is shown on Figure 8. Union Park discharged four times during this monitoring period. It does not appear that these discharges affect bacterial levels, Enterococcus values were high without any of these discharges. Water quality data collected by MWRA showed that high bacteria counts occurred regularly in Boston Harbor during 2019. Other potential sources of bacterial contamination to Boston Harbor include stormwater, illicit sanitary connections, pet and bird waste, bathers and illegal boat discharges. CSOs appear to be only one factor contributing to bacterial levels making it difficult to identify the source of contamination."
2019 CSO Monitoring Report, Boston Water and Sewer Commission, (June 2020)
"Stations 018, 019, 075, 138 and 178-Fort Point Channel. Although Fort Point Channel is not used for swimming, high bacterial counts are a concern and were measured frequently. Of the 98 samples collected, 30 were higher than 104/100 ml. At Station 075 near the BOS 070 outfall, 14 out of the 20 samples were above 104/100 ml. Water quality improved as the sample locations moved further away. Station 018 recorded 8 out of20 samples with elevated bacterial levels. Station 178 recorded 4 out of20 samples above 104/100 ml. The MWRA added Station 075 near the BOS 070 outfall and Station 178 at the Moakley Bridge in 2009 to provide data along the length of the channel. Several CSOs can discharge into this area, BOS 064, BOS 065, BOS 068, BOS 070, and BOS 073. The most active is BOS 070 which discharges flows from the MWRA's CSO Facility at Union Park Pumping Station. It should be noted that Union Park Pumping Station discharges are screened and disinfected prior to discharge into the Roxbury Canal Conduit. Water quality data collected by MWRA showed that high bacte1ia counts occurred regularly in Boston Harbor during 2020. Other potential sources of bacterial contamination to Boston Harbor include stormwater, illicit sanitary connections, pet and bird waste, bathers and illegal boat discharges. CSOs appear to be only one factor contributing to bacterial levels making it difficult to identify the source of contamination."
2020 CSO Monitoring Report, Boston Water and Sewer Commission, (April 2021)
"Stations 018, 019, 075, 138 and 178 - Fort Point Channel. Although Fort Point Channel is not used for swimming, high bacterial counts are a concern and were measured frequently. Of the 108 samples collected, 12 were higher than 104/100 ml. At Station 075 near the BOS 070 outfall, 3 out of the 20 samples were above 104/100 ml. Water quality improved as the sample locations moved further away. Station 178 recorded 2 out of21 samples above 104/100 ml. The MWRA added Station 075 near the BOS 070 outfall and Station 178 at the Moakley Bridge in 2009 to provide data along the length of the channel. Several CSOs can discharge into this area, BOS 064, BOS 065, BOS 068, BOS 070, and BOS 073. The most active is BOS 070 which discharges flows from the MWRA's CSO Facility at Union Park Pumping Station. It should be noted that Union Park Pumping Station discharges are screened and disinfected prior to discharge into the Roxbury Canal Conduit."
2021 CSO Monitoring Report, Boston Water and Sewer Commission, (2022)
"Although Fort Point Channel is not used for swimming, high bacterial counts are a concern and were measured frequently. Of the 104 samples collected, 22 were higher than 104/100 ml. At Station 075 near the BOS 070 outfall, 8 out of the 20 samples were above 104/100 ml. Water quality improved as the sample locations moved further away. Station 178 recorded 5 out of 20 samples above 104/100 ml. Several CSOs can discharge into this area, BOS 064, BOS 065, BOS 068, BOS 070, and BOS 073. The most active is BOS 070 which discharges flows from the MWRA's CSO Facility at Union Park Pumping Station. It should be noted that Union Park Pumping Station discharges are screened and disinfected prior to discharge into the Roxbury Canal Conduit. Very little correlation exists between rainfall and bacterial contamination."
2024 CSO Monitoring Report, Boston Water and Sewer Commission (April 2025).
"In Fort Point Channel, about one-quarter of an inch of rain would, on average, raise the fecal coliform count above the 200 colonies/100 ml water quality standard, while at the mouth of the inner harbor, near the airport, it would, on average, take more than two inches of rain before fecal coliform counts would exceed standards."
Combined Sewer Overflow Receiving Water Monitoring Boston Harbor and Its Tributary Rivers October 1990-September 1991 (January 1993).
"The South Station site and immediate area are located on filled tidelands, initially built beginning in the early part of the 19th century with the construction of wharves and piers along the western shoreline of Fort Point Channel. Boston Inner Harbor is included on the 2012 Final Integrated List of Waters as Category 5 and impaired for polychlorinated biphenyls (PCBs) in fish tissue, fecal coliform, enterococcus, dissolved oxygen, and other impairments, and requires one or more TMDL."
South Station Expansion, Draft Environmental Impact Report: Chapter 4 – Potential Environmental Impacts and Mitigation, Massachusetts Department of Transportation (October 2014).
"Stations 018, 019, 075, 138 and 178-Fort Point Channel. Although Fort Point Channel is not used for swimming, high bacterial counts are a concern and were measured frequently. Of the 105 samples collected, 26 were higher than 104/100 ml. At Station 075 near the BOS 070 outfall, 15 out of the 19 samples were above 104/ 100 ml. Water quality improved as the sample locations moved further away. Station 018 recorded 6 out of 20 samples with elevated bacterial levels. None of the samples in Inner Harbor Stations 019 and 138 exceeded standards. The MWRA added Station 075 near the BOS 070 outfall and Station 178 at the Moakley Bridge in 2009 to provide data along the length of the channel. Several CSOs can discharge into this area, BOS 064, BOS 065, BOS 068, BOS 070, and BOS 073. The most active is BOS 070 which discharges flows from the MWRA's CSO Facility at Union Park Pumping Station. It should be noted that Union Park Pumping Station discharges are screened and disinfected prior to discharge into the Roxbury Canal Conduit. A plot of Enterococcus bacteria counts is shown on Figure 8. Union Park discharged four times during this monitoring period. It does not appear that these discharges affect bacterial levels, Enterococcus values were high without any of these discharges. Water quality data collected by MWRA showed that high bacteria counts occurred regularly in Boston Harbor during 2019. Other potential sources of bacterial contamination to Boston Harbor include stormwater, illicit sanitary connections, pet and bird waste, bathers and illegal boat discharges. CSOs appear to be only one factor contributing to bacterial levels making it difficult to identify the source of contamination."
2019 CSO Monitoring Report, Boston Water and Sewer Commission, (June 2020)
"Stations 018, 019, 075, 138 and 178-Fort Point Channel. Although Fort Point Channel is not used for swimming, high bacterial counts are a concern and were measured frequently. Of the 98 samples collected, 30 were higher than 104/100 ml. At Station 075 near the BOS 070 outfall, 14 out of the 20 samples were above 104/100 ml. Water quality improved as the sample locations moved further away. Station 018 recorded 8 out of20 samples with elevated bacterial levels. Station 178 recorded 4 out of20 samples above 104/100 ml. The MWRA added Station 075 near the BOS 070 outfall and Station 178 at the Moakley Bridge in 2009 to provide data along the length of the channel. Several CSOs can discharge into this area, BOS 064, BOS 065, BOS 068, BOS 070, and BOS 073. The most active is BOS 070 which discharges flows from the MWRA's CSO Facility at Union Park Pumping Station. It should be noted that Union Park Pumping Station discharges are screened and disinfected prior to discharge into the Roxbury Canal Conduit. Water quality data collected by MWRA showed that high bacte1ia counts occurred regularly in Boston Harbor during 2020. Other potential sources of bacterial contamination to Boston Harbor include stormwater, illicit sanitary connections, pet and bird waste, bathers and illegal boat discharges. CSOs appear to be only one factor contributing to bacterial levels making it difficult to identify the source of contamination."
2020 CSO Monitoring Report, Boston Water and Sewer Commission, (April 2021)
"Stations 018, 019, 075, 138 and 178 - Fort Point Channel. Although Fort Point Channel is not used for swimming, high bacterial counts are a concern and were measured frequently. Of the 108 samples collected, 12 were higher than 104/100 ml. At Station 075 near the BOS 070 outfall, 3 out of the 20 samples were above 104/100 ml. Water quality improved as the sample locations moved further away. Station 178 recorded 2 out of21 samples above 104/100 ml. The MWRA added Station 075 near the BOS 070 outfall and Station 178 at the Moakley Bridge in 2009 to provide data along the length of the channel. Several CSOs can discharge into this area, BOS 064, BOS 065, BOS 068, BOS 070, and BOS 073. The most active is BOS 070 which discharges flows from the MWRA's CSO Facility at Union Park Pumping Station. It should be noted that Union Park Pumping Station discharges are screened and disinfected prior to discharge into the Roxbury Canal Conduit."
2021 CSO Monitoring Report, Boston Water and Sewer Commission, (2022)
"Although Fort Point Channel is not used for swimming, high bacterial counts are a concern and were measured frequently. Of the 104 samples collected, 22 were higher than 104/100 ml. At Station 075 near the BOS 070 outfall, 8 out of the 20 samples were above 104/100 ml. Water quality improved as the sample locations moved further away. Station 178 recorded 5 out of 20 samples above 104/100 ml. Several CSOs can discharge into this area, BOS 064, BOS 065, BOS 068, BOS 070, and BOS 073. The most active is BOS 070 which discharges flows from the MWRA's CSO Facility at Union Park Pumping Station. It should be noted that Union Park Pumping Station discharges are screened and disinfected prior to discharge into the Roxbury Canal Conduit. Very little correlation exists between rainfall and bacterial contamination."
2024 CSO Monitoring Report, Boston Water and Sewer Commission (April 2025).
(BWSC, 2025).
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(BWSC, 2025).
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Sewage Ecology
"Pollution by organic matter is not a simple problem, as it includes effects due to oxidizable materials, nutrients derived from their breakdown, and a significant amount of suspended solids. In most cases, and in our present state of knowledge, we can only partially disentangle the effects of these various factors from one another. Oxidizable materials discharged to the marine environment consist mainly of biodegradable organic materials, together with small amounts of inorganic reducing agents. The immediate effect of both of these types of substance is to reduce the amount of oxygen present in the water; the former by providing an energy source for micro-organisms which use oxygen to respire, the latter by simple chemical action.
Reish (1960) found that the effect of the discharge of domestic waste into Los Angeles and Long Beach harbours was to reduce the diversity of the benthic fauna and to encourage the presence of the polychaete Capitella capitata. Similar results associating C. capitata with the presence of organic wastes had been reported by Filice (I954) in San Francisco Bay and by Kitamori & Kobe (I959) in Japanese bays. Reish's findings, regarding both the diversity of benthic fauna and the association of C. capitata with polluted conditions, have since been confirmed by a number of other workers.
Tulkki (I968), in his study of the effect of pollution by town sewage on the benthos off Gothenburg, found a tendency for the areas of greatest faunal diversity to move away from the polluted zone. At a station within the city, thirteen marine euryhaline species occurred in 1922. In 1938 only two polychaetes, Eteone lonya and Nereis diversicolor, were found; and in 1965 only two oligochaetes were found at the same locality. 2.8 km down the fiord, fourteen marine benthic species and three littoral forms were found in 1912, while in 1922 a total of only nine species occurred. Further down the fiord, but still just within the polluted harbour area, it was found that the number of benthic species had increased during the present century. There were two species present in 1922, eleven in 1938, twenty in 1946 and twenty-seven in 1965. Among the species which appeared were Mya arenaria, Cardium lamarcki, Corophium volutator and Paramphiascopsis longirostris (Harpacticoida). Capitella capitata was present in large numbers after 1922. It is interesting to note that an increase in macro-faunal diversity has also been recently reported from a slightly polluted zone in Morecambe Bay, a large sandy intertidal area on the northwest coast of England.
Another species of polychaete also associated with pollution is the spionid Polydora ciliata. It has been observed in great numbers in the harbour of Bergen by Nair (I962), in Ostend by Persoone & de Pauw (I968), and within the harbour area of Gothenburg (up to a density of 7250 individuals per square metre) by Tulkki (I968). Occurring in the same area in large numbers was a second spionid species Scolelepis fuliginosa. This association of both Polydora ciliata and Scolelepis fuliginosa with polluted situations was also noted by Smyth (I968) in the Firth of Forth. Here, on a shore polluted by domestic sewage and gas works effluent, Polydora ciliata formed dense mats on low-level rocks; and in the close vicinity, Scolelepis fuliginosa occurred in high densities in the mud. Another mat-forming polychaete Fabricia sabella was common on rocks higher up on the shore. F. sabella was also found to thrive in a polluted part of Ostend harbour by Persoone & de Pauw (I968).
Those authors also examined the meiofauna in the same area of Ostend harbour and found that harpacticid copepods were very abundant, occurring in densities of 100 000 to 150 000 per square metre. The dominant species was always Nitocra typica, though Tisbe furcata occurred in large numbers during spring. Nematodes were exceptionally abundant; the numbers per cubic centimetre of mud were between 1000 and 2000, with a maximum of 7000. They found that the ciliates were the most important group, however, 55 species occurring in the Polydora ciliata mat (Aufwuchs). It is interesting to note here that J. R. Date has found, in his study of polluted beaches on the North Wirral coast in Liverpool Bay, that ciliates are less affected by pollution than the metazoa. Any reduction in diversity which he found could be attributed to a reduction in the number of metazoan species; the protozoa were similar in both polluted and unpolluted areas.
In considering the overall effects of organic pollution on benthic fauna, it may be useful to use the arrangement suggested by Tulkki (I968) in which he divided the affected species into three groups:
Beyer (I968) and Oliff et al. (I967) propose similar groups of species as indicators of polluted, semi-polluted and healthy conditions. The latter authors recommend, in addition, a number of chemical indicators.
A brief mention of bacteria and plankton may help to provide a concluding illustration of the effect of organic pollution on the marine environment. Sewage contains large numbers of bacteria of intestinal and other origin, but in addition the organic matter it contains will have an effect upon the bacteria in the receiving water. Persoone & de Pauw (I968) determined the number of estuarine bacteria, i.e. bacteria able to grow on a medium prepared with seawater, in different parts of the polluted Ostend harbour. Highest numbers (up to 830,000/ml) were found at the mouth of the sewers, in two polluted canals (about 200,000/ml and 50 000/ml), and on a beach close to the harbour mouth over which the ebb tide from the harbour passes (100,000/ml). One kilometre further, the number of bacteria decreased to about 8000/ml. For comparison, in the North Sea figures from a few thousands to 10 000/ml are given by Gunkel (I964).
The effects of sewage pollution on plankton have been noted in the Oslofiord by Beyer (I968). At the most heavily polluted station, Oslo harbour, exceedingly high concentrations of polychaete larvae, particularly Polydora ciliata, were found. An oceanic species, Aglanthe digitale (Trachymedusae), showed a steady increase up the fiord from about 30 individuals per 100 m3 of water at Drobak approximately 20 km from Oslo, to about 1600 per 100 m3 in the innermost basin of the fiord which is heavily polluted. Rathkea octopunctata showed a similar trend. On the other hand, Sagitta elegans, S. setosa and Calanus finmarchicus were much less abundant in the inner polluted areas.
Among the phytoplankton groups whose proliferation has been associated with high nutrient concentrations are flagellates, diatoms and Cyanophyceae. Excessive growth or 'blooms' of these organisms can be either directly toxic to fish or they can cause fish-kills by their decay and subsequent deoxygenation of the water. A further type of pollution occurs when masses of the planktonic material drift ashore to decay on the beaches-a phenomenon that takes place several times each year on the coasts of North Wales and Lancashire, and has also been recorded on the coast of Florida. One of the species responsible for blooms and beach-pollution in the Eastern Irish Sea is Phaeocystis, and according to Jones & Haq (I963) there is evidence that an essential growth factor for this organism is provided by pollution or run-off from terrestrial sources. Noctiluca scintillans has been also found to bloom in the area; in 1967 a bloom of it off Morecambe Bay was found to contain 1.4 million individuals per litre of water (O'Sullivan I967). According to T. J. Hart this was equivalent to 20 % of the volume of sample being occupied by Noctiluca and probably indicated concentration by wind and other factors, and senescence of the bloom.
The toxic properties of dinoflagellate blooms can also be the cause of ecological effects of considerable importance. According to Korringa (I968) dinoflagellates are the cause of conditions detrimental to the settling of oyster larvae in the Oosterschelde. In this country, Croft (I965) reported a local but severe irritation of littoral and sublittoral marine animals, which, from his description, was the result of a dinoflagellate bloom. Several species of toxin-producing dinoflagellates can be filtered by mussels or other shellfish which, if eaten, cause gastrointestinal disorders or paralytic shell-fish poisoning in man. Korringa (I968) lists several occurrences of such poisoning, and points out that in nearly all cases it has been connected with eutrophic conditions.
Eutrophic effects on attached algae are less common, though Sawyer (I965) describes a problem in Boston harbour as a result of excess growth of Ulva lactuca which he ascribes to nutrients derived from domestic waste. In Chesapeake Bay U. lactuca also appeared to be excessively prevalent in areas receiving domestic waste, and caused secondary pollution due to its becoming detached from the substrate and concentrated by wind and tide. The resulting decomposition products caused the water to become opaque and creamy in colour, and oxygen to fall as low as 4.1 parts/106. The hydrogen sulphide liberated during decomposition caused local complaints, and mortality of fish was also reported (Hanks I966)."
"Pollution by inert sewage-derived solids can also give rise to undesirable effects, particularly in estuaries and nearshore coastal waters. Very little work appears to have been done on this aspect of waste disposal ecology compared with the amount done on the diffusion and dispersion of the soluble portions of the waste. The behaviour of the suspended solids can be quite different from that of dissolved material such as nutrients, or bio-degradable material such as organic matter.
n the case of dissolved material, water movements cause a net transport from regions of high concentration to regions of low concentration, generally resulting in dilution and transport away from estuaries and coastal zones. In the case of suspended matter the reverse often occurs, and the material may be trapped and accumulated in the nearshore environment. For fine-grained material the minimum current velocity needed to pick it up (erosion or scour velocity) is considerably greater than the minimum velocity necessary to keep it in suspension (critical deposition velocity). This factor, acting in conjunction with estuarine circulation, sets up a sediment trap in which water is able to flow seaward, but particles heavier than water are retained and deposited as mud banks (Postma I967).
The biological effects of inert suspended solids in sewage wastes cannot be dis- entangled from the effects of accompanying organic matter and nutrients. It is only from a consideration of the effects of industrial wastes and from theoretical and laboratory work that such effects can be isolated. The two principal effects are: (i) the smothering of benthic animals including filter and detritus feeders, and (ii) the absorption of light and reduction of photosynthesis by phytoplankton. Experimental and geochemical evidence also shows that a large variety of dissolved organic substances may be absorbed by clay minerals which form part of the suspended solids present in sewage (Postma I967). Dissolved inorganic materials such as trace metals are also accumulated in clay minerals as well as in iron hydroxides, dead organic material and living plankton."
A. J. O'Sullivan, Ecological Effects of Sewage Discharge in the Marine Environment, Proceedings of the Royal Society of London. Series B, Biological Sciences , Apr. 13, 1971, Vol. 177, No. 1048, A Discussion on Biological Effects of Pollution in the Sea (Apr. 13, 1971), pp. 331-351.
Reish (1960) found that the effect of the discharge of domestic waste into Los Angeles and Long Beach harbours was to reduce the diversity of the benthic fauna and to encourage the presence of the polychaete Capitella capitata. Similar results associating C. capitata with the presence of organic wastes had been reported by Filice (I954) in San Francisco Bay and by Kitamori & Kobe (I959) in Japanese bays. Reish's findings, regarding both the diversity of benthic fauna and the association of C. capitata with polluted conditions, have since been confirmed by a number of other workers.
Tulkki (I968), in his study of the effect of pollution by town sewage on the benthos off Gothenburg, found a tendency for the areas of greatest faunal diversity to move away from the polluted zone. At a station within the city, thirteen marine euryhaline species occurred in 1922. In 1938 only two polychaetes, Eteone lonya and Nereis diversicolor, were found; and in 1965 only two oligochaetes were found at the same locality. 2.8 km down the fiord, fourteen marine benthic species and three littoral forms were found in 1912, while in 1922 a total of only nine species occurred. Further down the fiord, but still just within the polluted harbour area, it was found that the number of benthic species had increased during the present century. There were two species present in 1922, eleven in 1938, twenty in 1946 and twenty-seven in 1965. Among the species which appeared were Mya arenaria, Cardium lamarcki, Corophium volutator and Paramphiascopsis longirostris (Harpacticoida). Capitella capitata was present in large numbers after 1922. It is interesting to note that an increase in macro-faunal diversity has also been recently reported from a slightly polluted zone in Morecambe Bay, a large sandy intertidal area on the northwest coast of England.
Another species of polychaete also associated with pollution is the spionid Polydora ciliata. It has been observed in great numbers in the harbour of Bergen by Nair (I962), in Ostend by Persoone & de Pauw (I968), and within the harbour area of Gothenburg (up to a density of 7250 individuals per square metre) by Tulkki (I968). Occurring in the same area in large numbers was a second spionid species Scolelepis fuliginosa. This association of both Polydora ciliata and Scolelepis fuliginosa with polluted situations was also noted by Smyth (I968) in the Firth of Forth. Here, on a shore polluted by domestic sewage and gas works effluent, Polydora ciliata formed dense mats on low-level rocks; and in the close vicinity, Scolelepis fuliginosa occurred in high densities in the mud. Another mat-forming polychaete Fabricia sabella was common on rocks higher up on the shore. F. sabella was also found to thrive in a polluted part of Ostend harbour by Persoone & de Pauw (I968).
Those authors also examined the meiofauna in the same area of Ostend harbour and found that harpacticid copepods were very abundant, occurring in densities of 100 000 to 150 000 per square metre. The dominant species was always Nitocra typica, though Tisbe furcata occurred in large numbers during spring. Nematodes were exceptionally abundant; the numbers per cubic centimetre of mud were between 1000 and 2000, with a maximum of 7000. They found that the ciliates were the most important group, however, 55 species occurring in the Polydora ciliata mat (Aufwuchs). It is interesting to note here that J. R. Date has found, in his study of polluted beaches on the North Wirral coast in Liverpool Bay, that ciliates are less affected by pollution than the metazoa. Any reduction in diversity which he found could be attributed to a reduction in the number of metazoan species; the protozoa were similar in both polluted and unpolluted areas.
In considering the overall effects of organic pollution on benthic fauna, it may be useful to use the arrangement suggested by Tulkki (I968) in which he divided the affected species into three groups:
- 1. Regressive species which disappeared or retreated from the polluted region. Among these were Nephthys hombergi, Eteone longa, Pectinaria (as Lagis) koreni, Diastylis rathkei, and most sponges, echinoderms and ascidians. Halicryptus spinulosus was one species that completely disappeared. To these could be added the animals listed above in Smyth (I968).
- 2. Transgressive species, which have spread in the direction of the polluted regions or which now occur there but were scarce or absent before pollution began. Tulkki lists the isopods Cyathura carinata and Idotea chelipes and the bivalve Nucula nitida. In very polluted areas could be added the polychaetes Capitella capitata, Polydora ciliata, Fabricia sabella together with Nematodes.
- 3. Indifferent species whose distribution had not changed very much since the onset of pollution. Examples given are Harmothoi imbricata, Cardium lamarckii, Mya arenaria and Corbula gibba. Corophium volutator, Eteone longa, Nereis diversicolor and Mytilus edulis could also be included in this list of tolerant species.
Beyer (I968) and Oliff et al. (I967) propose similar groups of species as indicators of polluted, semi-polluted and healthy conditions. The latter authors recommend, in addition, a number of chemical indicators.
A brief mention of bacteria and plankton may help to provide a concluding illustration of the effect of organic pollution on the marine environment. Sewage contains large numbers of bacteria of intestinal and other origin, but in addition the organic matter it contains will have an effect upon the bacteria in the receiving water. Persoone & de Pauw (I968) determined the number of estuarine bacteria, i.e. bacteria able to grow on a medium prepared with seawater, in different parts of the polluted Ostend harbour. Highest numbers (up to 830,000/ml) were found at the mouth of the sewers, in two polluted canals (about 200,000/ml and 50 000/ml), and on a beach close to the harbour mouth over which the ebb tide from the harbour passes (100,000/ml). One kilometre further, the number of bacteria decreased to about 8000/ml. For comparison, in the North Sea figures from a few thousands to 10 000/ml are given by Gunkel (I964).
The effects of sewage pollution on plankton have been noted in the Oslofiord by Beyer (I968). At the most heavily polluted station, Oslo harbour, exceedingly high concentrations of polychaete larvae, particularly Polydora ciliata, were found. An oceanic species, Aglanthe digitale (Trachymedusae), showed a steady increase up the fiord from about 30 individuals per 100 m3 of water at Drobak approximately 20 km from Oslo, to about 1600 per 100 m3 in the innermost basin of the fiord which is heavily polluted. Rathkea octopunctata showed a similar trend. On the other hand, Sagitta elegans, S. setosa and Calanus finmarchicus were much less abundant in the inner polluted areas.
Among the phytoplankton groups whose proliferation has been associated with high nutrient concentrations are flagellates, diatoms and Cyanophyceae. Excessive growth or 'blooms' of these organisms can be either directly toxic to fish or they can cause fish-kills by their decay and subsequent deoxygenation of the water. A further type of pollution occurs when masses of the planktonic material drift ashore to decay on the beaches-a phenomenon that takes place several times each year on the coasts of North Wales and Lancashire, and has also been recorded on the coast of Florida. One of the species responsible for blooms and beach-pollution in the Eastern Irish Sea is Phaeocystis, and according to Jones & Haq (I963) there is evidence that an essential growth factor for this organism is provided by pollution or run-off from terrestrial sources. Noctiluca scintillans has been also found to bloom in the area; in 1967 a bloom of it off Morecambe Bay was found to contain 1.4 million individuals per litre of water (O'Sullivan I967). According to T. J. Hart this was equivalent to 20 % of the volume of sample being occupied by Noctiluca and probably indicated concentration by wind and other factors, and senescence of the bloom.
The toxic properties of dinoflagellate blooms can also be the cause of ecological effects of considerable importance. According to Korringa (I968) dinoflagellates are the cause of conditions detrimental to the settling of oyster larvae in the Oosterschelde. In this country, Croft (I965) reported a local but severe irritation of littoral and sublittoral marine animals, which, from his description, was the result of a dinoflagellate bloom. Several species of toxin-producing dinoflagellates can be filtered by mussels or other shellfish which, if eaten, cause gastrointestinal disorders or paralytic shell-fish poisoning in man. Korringa (I968) lists several occurrences of such poisoning, and points out that in nearly all cases it has been connected with eutrophic conditions.
Eutrophic effects on attached algae are less common, though Sawyer (I965) describes a problem in Boston harbour as a result of excess growth of Ulva lactuca which he ascribes to nutrients derived from domestic waste. In Chesapeake Bay U. lactuca also appeared to be excessively prevalent in areas receiving domestic waste, and caused secondary pollution due to its becoming detached from the substrate and concentrated by wind and tide. The resulting decomposition products caused the water to become opaque and creamy in colour, and oxygen to fall as low as 4.1 parts/106. The hydrogen sulphide liberated during decomposition caused local complaints, and mortality of fish was also reported (Hanks I966)."
"Pollution by inert sewage-derived solids can also give rise to undesirable effects, particularly in estuaries and nearshore coastal waters. Very little work appears to have been done on this aspect of waste disposal ecology compared with the amount done on the diffusion and dispersion of the soluble portions of the waste. The behaviour of the suspended solids can be quite different from that of dissolved material such as nutrients, or bio-degradable material such as organic matter.
n the case of dissolved material, water movements cause a net transport from regions of high concentration to regions of low concentration, generally resulting in dilution and transport away from estuaries and coastal zones. In the case of suspended matter the reverse often occurs, and the material may be trapped and accumulated in the nearshore environment. For fine-grained material the minimum current velocity needed to pick it up (erosion or scour velocity) is considerably greater than the minimum velocity necessary to keep it in suspension (critical deposition velocity). This factor, acting in conjunction with estuarine circulation, sets up a sediment trap in which water is able to flow seaward, but particles heavier than water are retained and deposited as mud banks (Postma I967).
The biological effects of inert suspended solids in sewage wastes cannot be dis- entangled from the effects of accompanying organic matter and nutrients. It is only from a consideration of the effects of industrial wastes and from theoretical and laboratory work that such effects can be isolated. The two principal effects are: (i) the smothering of benthic animals including filter and detritus feeders, and (ii) the absorption of light and reduction of photosynthesis by phytoplankton. Experimental and geochemical evidence also shows that a large variety of dissolved organic substances may be absorbed by clay minerals which form part of the suspended solids present in sewage (Postma I967). Dissolved inorganic materials such as trace metals are also accumulated in clay minerals as well as in iron hydroxides, dead organic material and living plankton."
A. J. O'Sullivan, Ecological Effects of Sewage Discharge in the Marine Environment, Proceedings of the Royal Society of London. Series B, Biological Sciences , Apr. 13, 1971, Vol. 177, No. 1048, A Discussion on Biological Effects of Pollution in the Sea (Apr. 13, 1971), pp. 331-351.
Plastic, synthetic ropes, natural fiber ropes, electrical cable insulations, and a wood panel were partially exposed in the black, bottom sediment of Port Hueneme Harbor to determine the effect of hydrogen sulfide on materials. After one year of exposure, the materials were recovered and examined for fouling and biodeterioration. In addition, hardness and moisture absorption tests were conducted on the plastic panels while tensile strength tests were conducted on rope specimens. Significant changes in hardness and moisture absorption were registered by nylon and phenolic laminate plastics. Decrease in tensile strength was experienced by all of the synthetic rope specimens. The natural rope specimens were totally destroyed by marine organisms. The wood panel was riddled by marine borers. An anaerobic environment devoid of oxygen and where marine sulfate-reducing bacteria flourish and produce hydrogen sulfide is found in many parts of the world's oceans. These areas are usually found in places where circulation of oxygenated seawater is restricted or reduced such as in harbors and bays (especially in bottom mud) and in basins (bottom waters of the Black Sea). In an anaerobic environment, the sulfate-reducing bacteria utilize sulfates and sulfites in the absence of oxygen during their metabolic process leading to the formation of hydrogen sulfide (rotten egg smell). The anaerobic corrosion of metals exposed in such an environment is widespread and destructive.
James S. Muraoka, EFFECT OF BOTTOM SEDIMENT CONTAINING HYDROGEN SULFIDE ON MATERIALS - PART I, Technical Note N-1263 (March 1973)
James S. Muraoka, EFFECT OF BOTTOM SEDIMENT CONTAINING HYDROGEN SULFIDE ON MATERIALS - PART I, Technical Note N-1263 (March 1973)
biota in inner/Outer Boston harbor pelagic zones
"Infaunal communities... from the innermost region, the Mystic and Chelsea Rivers, to the vicinity of the Reserved Channel... abundances are very low (<1,000/m2 ) to low (1,000–5,000/m2 ) and species numbers are also very small (<5/sample) or small (5–15/sample).
Polychaete, such as Nephtys incisa, Polydora cornuta, and Scoletoma fragilis, predominate among the few infaunal species present. MWRA sampling at the entrance to Fort Point channel, north of the Reserved Channel, has recorded new taxa from this area since 2004. However, the fauna has been dominated by the polychaete Nephtys cornuta (Maciolek et al., 2011)."
Final Supplemental Environmental Impact Statement and Final Environmental Impact Report (EOEA# 12958) for the Federal Deep Draft Navigation Improvement Project Boston Harbor, Massachusetts, U.S. Army Corps of Engineers & Massachusetts Port Authority (April 2013).
Polychaete, such as Nephtys incisa, Polydora cornuta, and Scoletoma fragilis, predominate among the few infaunal species present. MWRA sampling at the entrance to Fort Point channel, north of the Reserved Channel, has recorded new taxa from this area since 2004. However, the fauna has been dominated by the polychaete Nephtys cornuta (Maciolek et al., 2011)."
Final Supplemental Environmental Impact Statement and Final Environmental Impact Report (EOEA# 12958) for the Federal Deep Draft Navigation Improvement Project Boston Harbor, Massachusetts, U.S. Army Corps of Engineers & Massachusetts Port Authority (April 2013).
The harbor benthic faunal assemblages in the Inner Harbor area is known to consist of communities primarily made up of opportunistic deposit feeders such as polychaetas, amphipods, and shrimp associated with the harbor's organic sedimentation and silts. (Army, 1981a).
"There are approximately 1200 acres of salt marsh remaining within the Harbor. These areas are ecologically important because they contain suitable habitat for wildlife, function as nurseries for marine organisms, especially finfish, and are significant sources of vegetative biomass to the food chain of the Harbor estuary." (Army, 1980). "Marine life within the Harbor includes various types of phytoplankton (primarily diatoms and dinoflagellates) and zooplankton (mainly crustaceans). Benthic invertebrates vary considerably in distribution and numbers depending on environmental conditions, bottom sediments and available food supply." (Army, 1980).
Pelagic Fauna:
Inner & Outer Harbor Arthropoda:
Ampelisca,Carcinus maenas (Green Crab); Cancer irroratus (Rock Crab); Corophium sp. (Scud); Crangon septemspinosus (Sand Shrimp); Gammarus duebeni (Scud); Microdeutopus anomalus (Scud); Pandalus borealis (Pandalid Shrimp)
Inner & Outer Harbor Ichthyofauna:
"The Massachusetts Department of Marine Fisheries indicates that Fort Point Channel is considered habitat for larval settlement and juvenile development of winter flounder and that the channel may serve as refuge for migrating diadromous fish." (South Station Expansion DEIR, 2014).
"A variety of neoplasms and nonneoplastic hepatic lesions have been noted in winter flounder, Pseudopleuronectes americanus, from Boston Harbor, Massachusetts. Inflammatory lesions include cholangiitis, pericholangiitis, pericholangial fibrosis, hepatitis, and pancreatitis. Necrotic lesions consist essentially of focal coagulative necrosis and a distinctive vacuolated cell lesion of the hepatic parenchyma. The most conspicuous and numerous proliferative lesion is macrophage aggregate hyperplasia and hypertrophy. Preneoplastic lesions include principally basophilic foci of cellular alteration and hepatocellular adenoma. Carcinomas consist of several morphologic varieties: hepatocarcinoma, cholangiocarcinoma, and anaplastic adenocarcinoma."
Murchelano & Wolke, Neoplasms and Nonneoplastic Liver Lesions in Winter Flounder, Pseudopleuronectes americanus, from Boston Harbor, Massachusetts, Environmental Health Perspectives, Vol. 90 (Jan., 1991), pp. 17-26.
Inner & Outer Harbor Mollusca:
Crepidula fornicata & plana (Slipper limpet); Mya arenaria (Soft-shelled clam); Mytilus edulis (Blue mussel); Nassarius obsoletus; Tellina sp. (Tellin or Sunset shell).
"The softshelled clam (Mya arenaria) is the most important commercial shellfish within the Boston Harbor area. Blue mussels (Mytilus edulis) and duck clams (Macoma baltica) are also found in shellfish beds but are not harvested." (Army, 1981a).
Inner & Outer Harbor Annelida:
Aricidea, Capitella sp. (capitata, gracilis); Cistenides gouldii; Clymenella; Eteone longa; Harmonthoe imbricata; Microthamus abberaus; Myxicola infundibulum; Naidinae; Nepthys incisa (Shimmy worm); Nereis (diversicolor, succinea, virens ); Ophelia sp.; Pectinaria gouldii; Pharyx acutus; Phloe minuta; Phyllodoce (groenlandica, maculata, mucosa); Polydora (cifiata, cornuta, hamata, ligni, websteri); Polygordius; Scolelepis squamata; Scoletoma;Streblospio benedicti; Tharyx acutas; Tubificoides.
"Discharges of municipal and industrial wastes originating in the Boston metropolitan and harbor areas caused degraded water in all of Boston Harbor and associated bays inland from the harbor mouth near Massachusetts Bay. Deposition of nutrients from these wastes effected overly-abundant, pollution-indicating populations of polychaete worms that exceeded 200 per square foot in 34 square miles (80 percent) of Boston Harbor. About 14 square miles (30 percent) of Boston Harbor were grossly polluted as was suggested by polychaete worms that numbered 1,000 or more per square foot. Oily residues, foul odors, and suspended sewage-like particles often were apparent in most reaches of the harbor." (FWPCAb, 1968).
The Inner Harbor is polluted and provides an unsuitable environment for most types of benthic marine life. Gastropod and polychaete worms were the only types of benthic life present. The major polychaete type was Polydora ligni, a sedentary worm whose food source is organic deposits. Sediments of the Inner Harbor provided an almost inexhaustible food supply for this worm, while adverse substrate changes eliminated most of its predators and competitors. Results of the 1967 survey indicated polychaete densities of 964 per square foot. " (DOI, Joint Report, 1969).
Outer Harbor Cnidaria:
Aurelia aurita (Moon Jellyfish); Hydrozoa (unidentified);Metridium senile (Frilled Anemone); Abietinaria abietina; Bougainvillia (superciliaris); Cerianthus borealis; Edwardsia leganse; Gersemia fruticosa; Obelia geniculata; Pachycerianthus borealis; Thuiaria (similis); Tubularia; Urticina felina
Outer Harbor Tunicates:
Aplidium; Botryllus; Dendrodoa; Didemnum; Halocynthia pyriformis; Molgula
Outer Harbor Porifera:
Halichondria; Haliclona; Iophon; Polymastia
"There are approximately 1200 acres of salt marsh remaining within the Harbor. These areas are ecologically important because they contain suitable habitat for wildlife, function as nurseries for marine organisms, especially finfish, and are significant sources of vegetative biomass to the food chain of the Harbor estuary." (Army, 1980). "Marine life within the Harbor includes various types of phytoplankton (primarily diatoms and dinoflagellates) and zooplankton (mainly crustaceans). Benthic invertebrates vary considerably in distribution and numbers depending on environmental conditions, bottom sediments and available food supply." (Army, 1980).
Pelagic Fauna:
Inner & Outer Harbor Arthropoda:
Ampelisca,Carcinus maenas (Green Crab); Cancer irroratus (Rock Crab); Corophium sp. (Scud); Crangon septemspinosus (Sand Shrimp); Gammarus duebeni (Scud); Microdeutopus anomalus (Scud); Pandalus borealis (Pandalid Shrimp)
Inner & Outer Harbor Ichthyofauna:
"The Massachusetts Department of Marine Fisheries indicates that Fort Point Channel is considered habitat for larval settlement and juvenile development of winter flounder and that the channel may serve as refuge for migrating diadromous fish." (South Station Expansion DEIR, 2014).
"A variety of neoplasms and nonneoplastic hepatic lesions have been noted in winter flounder, Pseudopleuronectes americanus, from Boston Harbor, Massachusetts. Inflammatory lesions include cholangiitis, pericholangiitis, pericholangial fibrosis, hepatitis, and pancreatitis. Necrotic lesions consist essentially of focal coagulative necrosis and a distinctive vacuolated cell lesion of the hepatic parenchyma. The most conspicuous and numerous proliferative lesion is macrophage aggregate hyperplasia and hypertrophy. Preneoplastic lesions include principally basophilic foci of cellular alteration and hepatocellular adenoma. Carcinomas consist of several morphologic varieties: hepatocarcinoma, cholangiocarcinoma, and anaplastic adenocarcinoma."
Murchelano & Wolke, Neoplasms and Nonneoplastic Liver Lesions in Winter Flounder, Pseudopleuronectes americanus, from Boston Harbor, Massachusetts, Environmental Health Perspectives, Vol. 90 (Jan., 1991), pp. 17-26.
Inner & Outer Harbor Mollusca:
Crepidula fornicata & plana (Slipper limpet); Mya arenaria (Soft-shelled clam); Mytilus edulis (Blue mussel); Nassarius obsoletus; Tellina sp. (Tellin or Sunset shell).
"The softshelled clam (Mya arenaria) is the most important commercial shellfish within the Boston Harbor area. Blue mussels (Mytilus edulis) and duck clams (Macoma baltica) are also found in shellfish beds but are not harvested." (Army, 1981a).
Inner & Outer Harbor Annelida:
Aricidea, Capitella sp. (capitata, gracilis); Cistenides gouldii; Clymenella; Eteone longa; Harmonthoe imbricata; Microthamus abberaus; Myxicola infundibulum; Naidinae; Nepthys incisa (Shimmy worm); Nereis (diversicolor, succinea, virens ); Ophelia sp.; Pectinaria gouldii; Pharyx acutus; Phloe minuta; Phyllodoce (groenlandica, maculata, mucosa); Polydora (cifiata, cornuta, hamata, ligni, websteri); Polygordius; Scolelepis squamata; Scoletoma;Streblospio benedicti; Tharyx acutas; Tubificoides.
"Discharges of municipal and industrial wastes originating in the Boston metropolitan and harbor areas caused degraded water in all of Boston Harbor and associated bays inland from the harbor mouth near Massachusetts Bay. Deposition of nutrients from these wastes effected overly-abundant, pollution-indicating populations of polychaete worms that exceeded 200 per square foot in 34 square miles (80 percent) of Boston Harbor. About 14 square miles (30 percent) of Boston Harbor were grossly polluted as was suggested by polychaete worms that numbered 1,000 or more per square foot. Oily residues, foul odors, and suspended sewage-like particles often were apparent in most reaches of the harbor." (FWPCAb, 1968).
The Inner Harbor is polluted and provides an unsuitable environment for most types of benthic marine life. Gastropod and polychaete worms were the only types of benthic life present. The major polychaete type was Polydora ligni, a sedentary worm whose food source is organic deposits. Sediments of the Inner Harbor provided an almost inexhaustible food supply for this worm, while adverse substrate changes eliminated most of its predators and competitors. Results of the 1967 survey indicated polychaete densities of 964 per square foot. " (DOI, Joint Report, 1969).
Outer Harbor Cnidaria:
Aurelia aurita (Moon Jellyfish); Hydrozoa (unidentified);Metridium senile (Frilled Anemone); Abietinaria abietina; Bougainvillia (superciliaris); Cerianthus borealis; Edwardsia leganse; Gersemia fruticosa; Obelia geniculata; Pachycerianthus borealis; Thuiaria (similis); Tubularia; Urticina felina
Outer Harbor Tunicates:
Aplidium; Botryllus; Dendrodoa; Didemnum; Halocynthia pyriformis; Molgula
Outer Harbor Porifera:
Halichondria; Haliclona; Iophon; Polymastia
MWRA, 2022 OUTFALL MONITORING OVERVIEW, EQD Report 9/2023
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MWRA, 2023 OUTFALL MONITORING OVERVIEW, EQD Report 9/2024
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MWRA, 2022 OUTFALL MONITORING OVERVIEW, EQD Report 9/2023
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MWRA, 2023 OUTFALL MONITORING OVERVIEW, EQD Report 9/2024
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Phytoplankton & Floating Flora:
The eelgrass meadows in Boston Harbor had all but vanished by the late 1980’s, due to turbid water, viral diseases, and excessive nutrients that promote the growth of algae on seagrass leaves. Boston Harbor now supports only small areas of seagrasses in Hingham Bay in the area near Logan Airport (MWRA, 2004).
Inner & Outer Harbor Bryozoa:
Bugula; Electra; Membranipora membranacea
Inner & Outer Harbor Eumetazoa:
Platyhelminthes
The eelgrass meadows in Boston Harbor had all but vanished by the late 1980’s, due to turbid water, viral diseases, and excessive nutrients that promote the growth of algae on seagrass leaves. Boston Harbor now supports only small areas of seagrasses in Hingham Bay in the area near Logan Airport (MWRA, 2004).
Inner & Outer Harbor Bryozoa:
Bugula; Electra; Membranipora membranacea
Inner & Outer Harbor Eumetazoa:
Platyhelminthes
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Inner & Outer Harbor Plankton:
The phytoplankton of Boston Harbor exhibit regional, seasonal and annual changes in species and abundances related to changes in light, temperature, nutrients, water circulation and salinity. Generally the saltwater populations are dominated by the centric diatoms Skeletonema costata, Detonula confervacea, and Thallissiosira nordenskioldii, whereas freshwater inflows such as in the Mystic River are dominated by the freshwater diatom Asterionella formosa, green algae (Chlorophyceae) or blue-green algae (Cyanophyceae). Phytoplankton densities are generally considered relatively high due to the high organic loads. The Mystic River, Chelsea River and the Inner Harbor areas have higher population levels than the Outer Harbor. (Army, 1981a).
Zooplankton populations also exhibit regional, seasonal and annual differences based on the above stated physical and chemical factors as well as the phytoplankton distribution. Calanoid copepods such as Acartia clausi, A. tonsi, Centropages hamatus, and Eurytemora herdmani are dominant and exhibit seasonal changes during the year. A variety of less abundant zooplankton, planktonic eggs and larvae are also present. (Army, 1981a).
"Inorganic nutrients, ammonia nitrogen and soluble phosphorus, were greater than 100 and 40 micrograms per liter, respectively, in all reaches of Boston Harbor and adjacent bays inland from its mouth near Massachusetts Bay. These effected excessively dense populations of phytoplankton that averaged more than 1,000 per milliliter (indicative of overly enriched waters) in about 35 square miles (66 percent) of the harbor." (FWPCA, 1968b).
Identification of plankton indicated a normal seasonal dominance of the population by Chaetoceros sp. This diatom was replaced somewhat by Rhizosolenia sp. and Nitzschia sp. during the fall sampling indicating a species replacement that is normal with seasonal variations. All of these diatoms utilize nutrients such as phosphates and nitrates in their metabolic processes.
Joint Report on Pollution of Navigable Waters of Boston Harbor, US DOI and MA Water Resources Commission, April 1969
The phytoplankton of Boston Harbor exhibit regional, seasonal and annual changes in species and abundances related to changes in light, temperature, nutrients, water circulation and salinity. Generally the saltwater populations are dominated by the centric diatoms Skeletonema costata, Detonula confervacea, and Thallissiosira nordenskioldii, whereas freshwater inflows such as in the Mystic River are dominated by the freshwater diatom Asterionella formosa, green algae (Chlorophyceae) or blue-green algae (Cyanophyceae). Phytoplankton densities are generally considered relatively high due to the high organic loads. The Mystic River, Chelsea River and the Inner Harbor areas have higher population levels than the Outer Harbor. (Army, 1981a).
Zooplankton populations also exhibit regional, seasonal and annual differences based on the above stated physical and chemical factors as well as the phytoplankton distribution. Calanoid copepods such as Acartia clausi, A. tonsi, Centropages hamatus, and Eurytemora herdmani are dominant and exhibit seasonal changes during the year. A variety of less abundant zooplankton, planktonic eggs and larvae are also present. (Army, 1981a).
"Inorganic nutrients, ammonia nitrogen and soluble phosphorus, were greater than 100 and 40 micrograms per liter, respectively, in all reaches of Boston Harbor and adjacent bays inland from its mouth near Massachusetts Bay. These effected excessively dense populations of phytoplankton that averaged more than 1,000 per milliliter (indicative of overly enriched waters) in about 35 square miles (66 percent) of the harbor." (FWPCA, 1968b).
Identification of plankton indicated a normal seasonal dominance of the population by Chaetoceros sp. This diatom was replaced somewhat by Rhizosolenia sp. and Nitzschia sp. during the fall sampling indicating a species replacement that is normal with seasonal variations. All of these diatoms utilize nutrients such as phosphates and nitrates in their metabolic processes.
Joint Report on Pollution of Navigable Waters of Boston Harbor, US DOI and MA Water Resources Commission, April 1969
1998
Prokaryotic Communities:
"Waters overlying the shellfish beds are contaminated by wastes from sewage outfalls, resulting in the presence of coliform bacteria in the shellfish.: (Army, 1981a). "In 1967, excessive coliform bacteria, as great as 520,000 per 100 ml of water, were found in the Inner Harbor area." (FWPCA, 1968a).
"The bacterial quality of the harbor waters has been extensively investigated. There are many areas in the Inner and Outer Harbors which are considered grossly contaminated; and, in spite of the water classification of a particular area, the bacterial concentrations limit the harvesting of shellfish. High levels of bacteria have been found in the rivers which drain into the harbor, but the sources have never been documented." (Army, 1981b).
"The two most important water quality characteristics for Boston Harbor and adjacent waters, which bear upon their suitability for use are its content of bacteria and viruses. Because most diseases which are known to be transmitted through water are of intestinal origin and the source of the causative organisms in water is human excreta, the presence of sewage in water is evidence of the possibility of the presence of infectious organisms. Sanitary sewage, or the liquid discharges from the sanitary and domestic conveniences of dwellings, public buildings or industries, contains the waste products of man's life processes, including disease causing organisms or pathogens. At present, the best evidence of recent fecal pollution is the presence of coliform bacteria whose normal habitat is the lower intestines of warmblooded animals. About 100 to 400 billion coliform bacteria are excreted daily per person. These bacteria die off at about the same rate as pathogenic bacteria and therefore are measured as the indicator of pollution that is dangerous to the public health. The count of coliform bacteria is expressed in MPN (most probable number) per 100 ml (milliliter). Normal municipal sewage in dry weather contains about 50 to 300 million coliform bacteria per 100 ml. Standards of water quality discussed hereinafter assume that the numbers of infectious microorganisms of all types present at the source of pollution have been reduced at least in proportion to the reduction in the count of coliform bacteria. This assumption is probably warranted in the case of most pathogenic bacteria but is not warranted in the case of some viruses. Viruses are not removed by filtration to the same extent as bacteria, and some known viruses are more resistant to the usual dosages of chlorine. Among the other water quality characteristics which affect the sanitary quality of the Boston Harbor and adjacent waters and its suitability for various uses are dissolved oxygen content, biochemical oxygen demand (BOD), temperature, chloride content, chemical constituents, ammonia, presence of odor, scum, floating solids or debris and sludge deposits. In Boston Harbor and adjacent waters, the evidence of pollution may’ be indicated by any of these characteristics in various locations." (HUD, 1967).
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SOURCES: 2018 Boston Harbor Benthic Monitoring Report, Environmental Quality Report No. 2019-09, Massachusetts Water Resources Authority, (July 2019); South Station Expansion, Draft Environmental Impact Report: Chapter 4 – Potential Environmental Impacts and Mitigation, Massachusetts Department of Transportation (October 2014); Environmental Assessment for Maintenance Dredging Boston Harbor, Boston, Massachusetts, Dept. of the Army (Dec. 1981a); Environmental Assessment for Maintenance Dredging Boston Harbor, Boston, Massachusetts, Dept. of the Army (Dec. 1981b); Joint Report on Pollution of Navigable Waters of Boston Harbor, US DOI and MA Water Resources Commission, April 1969; The Navigable Waters of Boston Harbor, United States Department of the Interior, Federal Water Pollution Control Administration, Northeast Region, Boston, Massachusetts (May 1968a); United States Department of the Interior, Federal Water Pollution Control Administration, Biological Aspects of Water Quality Charles River and Boston Harbor, Massachusetts July-August 1967, (January 1968b); REPORT ON IMPROVEMENTS TO THE BOSTON MAIN DRAINAGE SYSTEM, Vol. 1, HUD Project No, P-Mass-—3306 Camp, Dresser, McKee (Sept. 1967); Literature Survey of Oceanographic Information Concerning Boston Harbor, Office of Naval Research, Woods Hole, Massachusetts, Reference No. 5 1- 84, (October 1951).
"Waters overlying the shellfish beds are contaminated by wastes from sewage outfalls, resulting in the presence of coliform bacteria in the shellfish.: (Army, 1981a). "In 1967, excessive coliform bacteria, as great as 520,000 per 100 ml of water, were found in the Inner Harbor area." (FWPCA, 1968a).
"The bacterial quality of the harbor waters has been extensively investigated. There are many areas in the Inner and Outer Harbors which are considered grossly contaminated; and, in spite of the water classification of a particular area, the bacterial concentrations limit the harvesting of shellfish. High levels of bacteria have been found in the rivers which drain into the harbor, but the sources have never been documented." (Army, 1981b).
"The two most important water quality characteristics for Boston Harbor and adjacent waters, which bear upon their suitability for use are its content of bacteria and viruses. Because most diseases which are known to be transmitted through water are of intestinal origin and the source of the causative organisms in water is human excreta, the presence of sewage in water is evidence of the possibility of the presence of infectious organisms. Sanitary sewage, or the liquid discharges from the sanitary and domestic conveniences of dwellings, public buildings or industries, contains the waste products of man's life processes, including disease causing organisms or pathogens. At present, the best evidence of recent fecal pollution is the presence of coliform bacteria whose normal habitat is the lower intestines of warmblooded animals. About 100 to 400 billion coliform bacteria are excreted daily per person. These bacteria die off at about the same rate as pathogenic bacteria and therefore are measured as the indicator of pollution that is dangerous to the public health. The count of coliform bacteria is expressed in MPN (most probable number) per 100 ml (milliliter). Normal municipal sewage in dry weather contains about 50 to 300 million coliform bacteria per 100 ml. Standards of water quality discussed hereinafter assume that the numbers of infectious microorganisms of all types present at the source of pollution have been reduced at least in proportion to the reduction in the count of coliform bacteria. This assumption is probably warranted in the case of most pathogenic bacteria but is not warranted in the case of some viruses. Viruses are not removed by filtration to the same extent as bacteria, and some known viruses are more resistant to the usual dosages of chlorine. Among the other water quality characteristics which affect the sanitary quality of the Boston Harbor and adjacent waters and its suitability for various uses are dissolved oxygen content, biochemical oxygen demand (BOD), temperature, chloride content, chemical constituents, ammonia, presence of odor, scum, floating solids or debris and sludge deposits. In Boston Harbor and adjacent waters, the evidence of pollution may’ be indicated by any of these characteristics in various locations." (HUD, 1967).
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SOURCES: 2018 Boston Harbor Benthic Monitoring Report, Environmental Quality Report No. 2019-09, Massachusetts Water Resources Authority, (July 2019); South Station Expansion, Draft Environmental Impact Report: Chapter 4 – Potential Environmental Impacts and Mitigation, Massachusetts Department of Transportation (October 2014); Environmental Assessment for Maintenance Dredging Boston Harbor, Boston, Massachusetts, Dept. of the Army (Dec. 1981a); Environmental Assessment for Maintenance Dredging Boston Harbor, Boston, Massachusetts, Dept. of the Army (Dec. 1981b); Joint Report on Pollution of Navigable Waters of Boston Harbor, US DOI and MA Water Resources Commission, April 1969; The Navigable Waters of Boston Harbor, United States Department of the Interior, Federal Water Pollution Control Administration, Northeast Region, Boston, Massachusetts (May 1968a); United States Department of the Interior, Federal Water Pollution Control Administration, Biological Aspects of Water Quality Charles River and Boston Harbor, Massachusetts July-August 1967, (January 1968b); REPORT ON IMPROVEMENTS TO THE BOSTON MAIN DRAINAGE SYSTEM, Vol. 1, HUD Project No, P-Mass-—3306 Camp, Dresser, McKee (Sept. 1967); Literature Survey of Oceanographic Information Concerning Boston Harbor, Office of Naval Research, Woods Hole, Massachusetts, Reference No. 5 1- 84, (October 1951).
"For more than 100 years, U.S. public health personnel have relied extensively on an indicator organism approach to assess the microbiological quality of drinking water. These bacterial indicator microorganisms (particularly “coliforms,” described later) are typically used to detect the possible presence of microbial contamination of drinking water by human waste. More specifically, fecal indicator bacteria provide an estimation of the amount of feces, and indirectly, the presence and quantity of fecal pathogens in the water.
Over the long history of their development and use, coliform test methods have been standardized, they are relatively easy and inexpensive to use, and enumeration of coliforms has proven to be a useful method for assessing sewage contamination of drinking water. In conjunction with chlorination to reduce coliform levels, this practice has led to a dramatic decrease in waterborne diseases such as cholera and typhoid fever. Furthermore, the use of bacterial indicators has been extended to U.S. “ambient” waters in recent decades—especially freshwater and marine-estuarine waters used for recreation."
National Research Council (US) Committee on Indicators for Waterborne Pathogens. Indicators for Waterborne Pathogens. Washington (DC): National Academies Press (US); 2004. 1, Introduction and Historical Background. Available from: https://www.ncbi.nlm.nih.gov/books/NBK215658/
Over the long history of their development and use, coliform test methods have been standardized, they are relatively easy and inexpensive to use, and enumeration of coliforms has proven to be a useful method for assessing sewage contamination of drinking water. In conjunction with chlorination to reduce coliform levels, this practice has led to a dramatic decrease in waterborne diseases such as cholera and typhoid fever. Furthermore, the use of bacterial indicators has been extended to U.S. “ambient” waters in recent decades—especially freshwater and marine-estuarine waters used for recreation."
National Research Council (US) Committee on Indicators for Waterborne Pathogens. Indicators for Waterborne Pathogens. Washington (DC): National Academies Press (US); 2004. 1, Introduction and Historical Background. Available from: https://www.ncbi.nlm.nih.gov/books/NBK215658/
Other Indicator Species in Boston Harbor
SEA LETTUCE
"Within recent years persons living near certain areas of Boston Harbor have been subjected to a new and highly undesirable odor problem. This has been related to extensive growths of an aquatic plant commonly referred to as "sea lettuce." During the late fifties there was increasing evidence of a sea lettuce problem in Winthrop Harbor. By the summer of 1961 conditions became so intolerable on occasion that home owners in some areas had to keep windows closed and some were forced to leave their homes to seek relief from the nauseous odors. Many homes with lead pigment paints were discolored. Town officials were distraught by a complaining populace and the threat of damage claims related to health and property.
In certain sea-side localities a nuisance at times of considerable magnitude is produced by the decomposition of masses of green seaweed, chiefly of the species Ulva latissima, but also of certain varieties of Enteromorpha, such as E. compressa and E. intestinalis and as will be shown, there is every reason to believe that the growth of these seaweeds in quantity, and especially that of the Ulva, may be traced to the pollution of the waters, in which they are found, by sewage. For a number of years a most serious nuisance of this kind has occurred in the upper reaches of Belfast Lough during the summer and autumn, the stench at low tide being often quite overpowering, and the air heavily charged with sulfuretted hydrogen.
Growths of sea lettuce are prevalent in three areas of Boston Harbor, namely, Winthrop Harbor, Squantum Bay, and along the shores of Nut Island in Quincy Bay. They have become public nuisances during the summer and autumn seasons to residents of Winthrop and Squantum be cause of the proximity of residences and unfavorable winds. The waters of Winthrop Bay were found to be highly contaminated by sewage discharges from an outfall sewer terminating in President Roads near Deer Island Light. Coliform and total bacterial numbers were excessive on occasion and the fertilizing elements, nitrogen and phosphorus, were present at levels far in excess of amounts in normal seawater at all times. It was concluded that sewage dis charges into tidal waters were directly responsible for furnishing the nutrients responsible for supporting the ex tensive growths of sea lettuce."
C. N. Sawyer, The Sea Lettuce Problem in Boston Harbor, Journal (Water Pollution Control Federation), Aug., 1965, Vol. 37, No. 8 (Aug., 1965), pp. 1122-1133
"Within recent years persons living near certain areas of Boston Harbor have been subjected to a new and highly undesirable odor problem. This has been related to extensive growths of an aquatic plant commonly referred to as "sea lettuce." During the late fifties there was increasing evidence of a sea lettuce problem in Winthrop Harbor. By the summer of 1961 conditions became so intolerable on occasion that home owners in some areas had to keep windows closed and some were forced to leave their homes to seek relief from the nauseous odors. Many homes with lead pigment paints were discolored. Town officials were distraught by a complaining populace and the threat of damage claims related to health and property.
In certain sea-side localities a nuisance at times of considerable magnitude is produced by the decomposition of masses of green seaweed, chiefly of the species Ulva latissima, but also of certain varieties of Enteromorpha, such as E. compressa and E. intestinalis and as will be shown, there is every reason to believe that the growth of these seaweeds in quantity, and especially that of the Ulva, may be traced to the pollution of the waters, in which they are found, by sewage. For a number of years a most serious nuisance of this kind has occurred in the upper reaches of Belfast Lough during the summer and autumn, the stench at low tide being often quite overpowering, and the air heavily charged with sulfuretted hydrogen.
Growths of sea lettuce are prevalent in three areas of Boston Harbor, namely, Winthrop Harbor, Squantum Bay, and along the shores of Nut Island in Quincy Bay. They have become public nuisances during the summer and autumn seasons to residents of Winthrop and Squantum be cause of the proximity of residences and unfavorable winds. The waters of Winthrop Bay were found to be highly contaminated by sewage discharges from an outfall sewer terminating in President Roads near Deer Island Light. Coliform and total bacterial numbers were excessive on occasion and the fertilizing elements, nitrogen and phosphorus, were present at levels far in excess of amounts in normal seawater at all times. It was concluded that sewage dis charges into tidal waters were directly responsible for furnishing the nutrients responsible for supporting the ex tensive growths of sea lettuce."
C. N. Sawyer, The Sea Lettuce Problem in Boston Harbor, Journal (Water Pollution Control Federation), Aug., 1965, Vol. 37, No. 8 (Aug., 1965), pp. 1122-1133
BBC, Seaweed suspected in French death (2009)
French investigators are examining whether a lorry driver has become the first victim of a toxic seaweed that is clogging parts of the Brittany coast. The driver died in July after carrying three truckloads of sea lettuce away from the beaches where it has been decaying, releasing poisonous gas. His death was originally recorded as a heart attack but prosecutors want to know if it was linked to the seaweed. France's PM warned of the health risk while visiting the beaches last month. Francois Fillon announced that the government would pay for cleaning up the beaches polluted by the sea lettuce, Ulva lactuca. Locals had raised the alarm after a horse, being ridden over the sands, collapsed and died. Its rider fell unconscious and had to be dragged off the algae-coated beach. By then, the lorry driver had already died. The 48-year-old driver had been working without a mask or gloves and died at the wheel of his vehicle when it crashed into a wall, reports Tim Finan in Brittany for the BBC. The man had been part of the annual operation to remove 2,000 tonnes of rotting sea lettuce from the beaches at Binic. His family have so far refused to allow an autopsy to establish the exact cause of his death, but on Monday the local prosecutor ordered a preliminary investigation. Researchers from France's National Institute for Environmental Technology and Hazards (Ineris) have visited the same beach and found hydrogen sulphide in such concentration that it could be "deadly in few minutes". Sea lettuce is harmless in the sea, but as it decomposes on the beach it releases the deadly gas. Environmentalists say decades of misuse of Brittany's agricultural land is to blame for the explosion of algae, due to the high levels of nitrates used in fertilisers and excreted by the region's high concentration of livestock.
French investigators are examining whether a lorry driver has become the first victim of a toxic seaweed that is clogging parts of the Brittany coast. The driver died in July after carrying three truckloads of sea lettuce away from the beaches where it has been decaying, releasing poisonous gas. His death was originally recorded as a heart attack but prosecutors want to know if it was linked to the seaweed. France's PM warned of the health risk while visiting the beaches last month. Francois Fillon announced that the government would pay for cleaning up the beaches polluted by the sea lettuce, Ulva lactuca. Locals had raised the alarm after a horse, being ridden over the sands, collapsed and died. Its rider fell unconscious and had to be dragged off the algae-coated beach. By then, the lorry driver had already died. The 48-year-old driver had been working without a mask or gloves and died at the wheel of his vehicle when it crashed into a wall, reports Tim Finan in Brittany for the BBC. The man had been part of the annual operation to remove 2,000 tonnes of rotting sea lettuce from the beaches at Binic. His family have so far refused to allow an autopsy to establish the exact cause of his death, but on Monday the local prosecutor ordered a preliminary investigation. Researchers from France's National Institute for Environmental Technology and Hazards (Ineris) have visited the same beach and found hydrogen sulphide in such concentration that it could be "deadly in few minutes". Sea lettuce is harmless in the sea, but as it decomposes on the beach it releases the deadly gas. Environmentalists say decades of misuse of Brittany's agricultural land is to blame for the explosion of algae, due to the high levels of nitrates used in fertilisers and excreted by the region's high concentration of livestock.
sludge & Microorganisms
Phosphorus in Sewage, Polluted Waters, Sludges, and Effluents (1996)
"Kelly, Sanderson, and Neidl (1961), during their study of the removal of enteroviruses from sewage by activated sludge, have indicated that phosphorus is an important factor in virus survival. Bush and Isherwood (1966) carried out experiments on the removal of the Coxsackie A-13 virus in sewage treatment, and found that the virus could be removed effectively when heavy flock loading was maintained in the activated sludge unit, but that the trickling filter did not perform as well. The phosphorus contents of the effluents from the activated sludge system and the trickling filter were 1-5 mg/I and 8 mg/I as PO4, respectively. The influent to these systems contained 5-9 mg/I as PO4. Klotter (1965) has investigated the capacity of activated sludge to remove the orthophosphates
and condensed phosphates from waste water.
Gabbano (1928) observed a large increase of B. coli (Escherichia coli) in certain mineral waters containing alkaline phosphates and alkaline earth phosphates along with nitrate and chloride; B. typhosus (Salmonella typhosa), however, disappeared in a few days. The unusually high bacterial counts in the water supplies of two towns in Massachusetts, after treatment with a proprietary mixture containing sodium hexametaphosphate, were traced to the influence of the phosphate. Experiments indicated that the hexametaphosphate, orthophosphate, and pyrophosphate stimulated bacterial growth to an increasing extent (McCarthy and Cassidy, 1943).
The abnormally high counts of E. coli in the various parts of the water distribution system of a city in Massachusetts (when the source of the supply contained only a few E. coli) were also found to be due to the use of phosphates for the control of corrosion of pipes. The coliform bacteria which grew readily in the presence of phosphates could be controlled if hypochlorite was added in amounts sufficient to maintain residual chlorine in the mains (Weston, 1944). There are also bacteria which can reduce phosphate to phosphite, hypophosphite, and eventually under anaerobic conditions to phosphine (PH3). The latter has been detected in some polluted waters (Klein, 1962).
E. G. Srinath and S. C. Pillai, Phosphorus in Sewage, Polluted Waters, Sludges, and Effluents, The Quarterly Review of Biology, Vol. 41, No. 4 (Dec., 1966), pp. 384-407
and condensed phosphates from waste water.
Gabbano (1928) observed a large increase of B. coli (Escherichia coli) in certain mineral waters containing alkaline phosphates and alkaline earth phosphates along with nitrate and chloride; B. typhosus (Salmonella typhosa), however, disappeared in a few days. The unusually high bacterial counts in the water supplies of two towns in Massachusetts, after treatment with a proprietary mixture containing sodium hexametaphosphate, were traced to the influence of the phosphate. Experiments indicated that the hexametaphosphate, orthophosphate, and pyrophosphate stimulated bacterial growth to an increasing extent (McCarthy and Cassidy, 1943).
The abnormally high counts of E. coli in the various parts of the water distribution system of a city in Massachusetts (when the source of the supply contained only a few E. coli) were also found to be due to the use of phosphates for the control of corrosion of pipes. The coliform bacteria which grew readily in the presence of phosphates could be controlled if hypochlorite was added in amounts sufficient to maintain residual chlorine in the mains (Weston, 1944). There are also bacteria which can reduce phosphate to phosphite, hypophosphite, and eventually under anaerobic conditions to phosphine (PH3). The latter has been detected in some polluted waters (Klein, 1962).
E. G. Srinath and S. C. Pillai, Phosphorus in Sewage, Polluted Waters, Sludges, and Effluents, The Quarterly Review of Biology, Vol. 41, No. 4 (Dec., 1966), pp. 384-407
Pollution in Estuaries and Coastal Marine Waters (1994)
"The oxidation of pollutant organic matter may produce acute oxygen deficiency in susceptible bodies of water. Two types of oxygen depletion zones have been differentiated in estuaries: (1) anoxic zones (bottom waters with <0.1 mg/1 dissolved oxygen); and (2) hypoxic zones (bottom waters < 2.0 mg/1 dissolved oxygen) (POKRYFKI and. RANDALL, 1987).
The most sensitive systems appear to be those characterized by poor circulation where oxygen-depleted waters cannot be effectively reoxygenated. These affected bodies often are poorly flushed shallow coastal bays characterized by low freshwater inflow and restricted tidal ranges (REYES and MERINO, 1991).
While enrichment with inorganic nutrients may in fact maintain healthy and productive biotic communities in some of these shallow coastal bays, excess nitrogen input has, in more than one case, generated phytoplankton blooms that have led to oxygen deficits in bottom waters, ultimately causing the death of much aquatic life.
Even larger estuaries (e.g., Chesapeake Bay and Long Island Sound) have fallen victim to hypoxia and anoxia, resulting in a series of undesirable effects and culminating in multiple fishkills and the loss of valuable shellfish beds (OFFICER et al., 1984; SELIGER et al., 1985; CORRELL, 1987; PARKER and O'REILLY, 1991; WELSH and ELLER, 1991).
Broad expanses of Chesapeake Bay experience anoxia in late spring and summer (OFFICER et al., 1984; SELIGER et al., 1985). The intensity of anoxia has been related to the degree of stratification of the water column and to the freshwater flow into the bay (TYLER, 1986).
Seasonal increases in density stratification of the estuary ascribable to the spring freshet foster water column stability and minimize advective transport of oxygen from the surface to the deep layer. These hydrographic conditions, together with the decomposition of phytoplankton and organic matter derived from sewage inputs and other sources (e.g., industrial outfalls), cause a decrease in dissolved oxygen."
Michael J. Kennish, Pollution in Estuaries and Coastal Marine Waters, Journal of Coastal Research, 1994, Special Issue No. 12. COASTAL HAZARDS: PERCEPTION, SUSCEPTIBILITY AND MITIGATION (1994), pp. 27-49
"The oxidation of pollutant organic matter may produce acute oxygen deficiency in susceptible bodies of water. Two types of oxygen depletion zones have been differentiated in estuaries: (1) anoxic zones (bottom waters with <0.1 mg/1 dissolved oxygen); and (2) hypoxic zones (bottom waters < 2.0 mg/1 dissolved oxygen) (POKRYFKI and. RANDALL, 1987).
The most sensitive systems appear to be those characterized by poor circulation where oxygen-depleted waters cannot be effectively reoxygenated. These affected bodies often are poorly flushed shallow coastal bays characterized by low freshwater inflow and restricted tidal ranges (REYES and MERINO, 1991).
While enrichment with inorganic nutrients may in fact maintain healthy and productive biotic communities in some of these shallow coastal bays, excess nitrogen input has, in more than one case, generated phytoplankton blooms that have led to oxygen deficits in bottom waters, ultimately causing the death of much aquatic life.
Even larger estuaries (e.g., Chesapeake Bay and Long Island Sound) have fallen victim to hypoxia and anoxia, resulting in a series of undesirable effects and culminating in multiple fishkills and the loss of valuable shellfish beds (OFFICER et al., 1984; SELIGER et al., 1985; CORRELL, 1987; PARKER and O'REILLY, 1991; WELSH and ELLER, 1991).
Broad expanses of Chesapeake Bay experience anoxia in late spring and summer (OFFICER et al., 1984; SELIGER et al., 1985). The intensity of anoxia has been related to the degree of stratification of the water column and to the freshwater flow into the bay (TYLER, 1986).
Seasonal increases in density stratification of the estuary ascribable to the spring freshet foster water column stability and minimize advective transport of oxygen from the surface to the deep layer. These hydrographic conditions, together with the decomposition of phytoplankton and organic matter derived from sewage inputs and other sources (e.g., industrial outfalls), cause a decrease in dissolved oxygen."
Michael J. Kennish, Pollution in Estuaries and Coastal Marine Waters, Journal of Coastal Research, 1994, Special Issue No. 12. COASTAL HAZARDS: PERCEPTION, SUSCEPTIBILITY AND MITIGATION (1994), pp. 27-49
"The ecology of purple sulfur bacteria in a sewage oxidation lagoon was investigated. The appearance of high populations of purple sulfur bacteria in a local oxidation sewage lagoon receiving municipal and industrial wastes initiated this ecological investigation. These nutrition while utilizing sulfide and certain other substrates as electron sources in the photosynthetic process.
Chemical changes in the lagoon were investigated by monitoring biochemical oxygen demand (BOD5), sulfide, sulfate, phosphate, total carbohydrates, volatile acids, alkalinity, and pH. Lagoon water temperatures were observed daily. Microbial ecological relationships were deduced by enumerating coliforms, total bacteria other than anaerobes [Tryptone Glucose Extract (TGE) agar], methane formers such as Methanobacteriumformicicum, sulfate reducers, purple sulfur bacteria, and algae. Finally, two strains of purple sulfur bacteria were characterized.
Two populations, purple sulfur bacteria and total bacteria (TGE agar), reached maximal concentrations in the warmest part of the 1967 summer. Purple sulfur bacteria reached maximal numbers as concentrations of sulfide and volatile acids were depleted, whereas carbohydrates and alkalinity remained unchanged. Low sulfate levels, which were not limiting for sulfate reducers, may be attributable to storage of sulfur within purple sulfur bacteria. No biological, chemical, or physical agent was linked to the removal of coliforms.
The increase of algae in the late summer of 1967 may have been related to the low organic content of the lagoon during this period. Although lagoon pH (7.7 to 8.2) was favorable for purple sulfur bacterial growth, temperatures and sulfides were not optimal in the lagoon for these organisms.
Chromatium vinosum and Thiocapsa floridana (the predominant lagoon purple sulfur organism in 1967 and 1968) utilized certain carbohydrates, amino acids, volatile acids, and Krebs cycle intermediates. Also purple sulfur bacteria lowered BOD levels as demonstrated by the growth of T. floridana in sterilized sewage."
Holm & Vennes, Occurrence of Purple Sulfur Bacteria in a Sewage Treatment Lagoon, APPLIED MICROBIOLOGY, Vol. 19, No. 6, June 1970, p. 988-996
Chemical changes in the lagoon were investigated by monitoring biochemical oxygen demand (BOD5), sulfide, sulfate, phosphate, total carbohydrates, volatile acids, alkalinity, and pH. Lagoon water temperatures were observed daily. Microbial ecological relationships were deduced by enumerating coliforms, total bacteria other than anaerobes [Tryptone Glucose Extract (TGE) agar], methane formers such as Methanobacteriumformicicum, sulfate reducers, purple sulfur bacteria, and algae. Finally, two strains of purple sulfur bacteria were characterized.
Two populations, purple sulfur bacteria and total bacteria (TGE agar), reached maximal concentrations in the warmest part of the 1967 summer. Purple sulfur bacteria reached maximal numbers as concentrations of sulfide and volatile acids were depleted, whereas carbohydrates and alkalinity remained unchanged. Low sulfate levels, which were not limiting for sulfate reducers, may be attributable to storage of sulfur within purple sulfur bacteria. No biological, chemical, or physical agent was linked to the removal of coliforms.
The increase of algae in the late summer of 1967 may have been related to the low organic content of the lagoon during this period. Although lagoon pH (7.7 to 8.2) was favorable for purple sulfur bacterial growth, temperatures and sulfides were not optimal in the lagoon for these organisms.
Chromatium vinosum and Thiocapsa floridana (the predominant lagoon purple sulfur organism in 1967 and 1968) utilized certain carbohydrates, amino acids, volatile acids, and Krebs cycle intermediates. Also purple sulfur bacteria lowered BOD levels as demonstrated by the growth of T. floridana in sterilized sewage."
Holm & Vennes, Occurrence of Purple Sulfur Bacteria in a Sewage Treatment Lagoon, APPLIED MICROBIOLOGY, Vol. 19, No. 6, June 1970, p. 988-996
worms in Dredged Blue Clay
From the 1940s to 1976, a majority of the Boston Harbor area's dredged material and other debris had been released at the Boston Lightship Disposal Site (BLDS). A 1994 study conducted a sediment-profile and plan view photographic survey of the Boston Lightship Disposal Site. "Recolonization of old dredged material has been extensive." (Camp, Dresser, and McKee, Inc. 1991).
MONITORING CRUISE AT THE BOSTON LIGHTHOUSE DISPOSAL SITE AUGUST 1994, CONTRIBUTION #113 (August 1996), Report No. SAIC No. 328, Science Applications International Corporation for U.S. Army Corps of Engineers.
MONITORING CRUISE AT THE BOSTON LIGHTHOUSE DISPOSAL SITE AUGUST 1994, CONTRIBUTION #113 (August 1996), Report No. SAIC No. 328, Science Applications International Corporation for U.S. Army Corps of Engineers.
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Silicon cycling
Human influences on global silicon (Si) cycling include land-use change, deforestation, and wastewater discharge. Here we quantified the effect of urban expansion and historic land fill on dissolved silica (DSi) concentrations in urban groundwater in a northern temperate city. We hypothesized that historical land use, fill material, and urban infrastructure buried below cities create a unique anthropogenic geology which acts as a DSi source. We found that concentrations of DSi in urban groundwater are significantly higher than those from non-urban environments. We also found that historic land-use variables out-perform traditional topographic variables predicting urban DSi concentrations. We show that higher groundwater DSi concentrations result in increased subterranean groundwater discharge (SGD) fluxes, thereby altering coastal receiving water DSi availability. Further, we demonstrate that accounting for urban SGD DSi fluxes globally, could increase DSi SGD export by 20%. Together these results call for a re-evaluation of anthropogenic impacts on the global Si cycle. Maguire, Timothy J, and Robinson W Fulweiler. “Urban groundwater dissolved silica concentrations are elevated due to vertical composition of historic land-filling.” The Science of the total environment vol. 684 (2019): 89-95. doi:10.1016/j.scitotenv.2019.05.272
