^2 ACIDIC PRECIPITATION IN ONTARIO STUDY (APIOS) ANNUAL PROGRAM REPORT 1988/1989 JANUARY 1990 Environment Environnement Ontario Jim Bradley, Minister/ministre ISSN: 0835-4383 (APIOS) 0835-4456 Program Report ACIDIC PRECIPITATION IN ONTARIO STUDY (APIOS) ANNUAL PROGRAM REPORT 1988/1989 JANUARY 1990 Copyright: Queen's Printer for Ontario, 1990 This publication may be reproduced for non-commercial purposes with appropriate attribution. TABLE OF CONTENTS Page LIST OF FIGURES v LIST OF TABLES vii INTRODUCTION 1 ATMOSPHERIC PROCESSES STUDIES A. Emissions Inventory 2 B. Modelling Studies 2 C. Deposition Monitoring Networks 8 D. Oxidants Strategy Development 11 E. Meteorological Studies 11 TERRESTRIAL EFFECTS STUDIES A. Vegetation Studies Mobile Rain Exclusion Canopies 13 a. Soybean Studies 13 b. Forest Tree Species Studies 13 Insect - Acidic Precipitation 14 B. Soil Studies Concentrations of Metals in Surface Soils 14 Sources of Variability in Soil Properties 15 C. Forest Productivity and Decline Studies Maple Decline Study 17 Hardwood Decline Studies 17 Hardwood Nutrition Studies 19 Remote Sensing 20 TABLE OF CONTENTS (continued) Page D. MNR Wildlife Studies Cadmium Accumulation by Aquatic Plants Preferred as Forage by Ontario Moose 21 BIOGEOCHEMISTRY STUDIES A. Biogeochemical Study Sites - Monitoring Programmes 22 B. Process Studies Bioaccumulation of Nutrients 24 Mineral Weathering Rates 24 Sulphur Adsorption Studies 25 Groundwater Studies 26 AQUATIC EFFECTS STUDIES A. Chemical Studies Calibrated Watersheds a. Chemical Limnology 27 b. Metal Contaminants 28 c. Extensive Lake Sampling 28 B. Biological Studies Lake pH - Algal Sediment Fossils 29 Filamentous Algae 29 Zooplankton 30 Invertebrates 50 Toxicity Studies 51 Biological Survey 52 Biological Monitoring 52 TABLE OF CONTENTS (continued) Page Metal and Organic Residue Monitoring a. Monitoring Mercury Levels in Yearling Yellow Perch 33 b. Investigating Relationships Between Mercury in Sport Fish and Lakewater Quality 33 MNR Fish Studies a. Occurrence of Cyprinids and Other Small Fish Species in Relation to pH in Ontario Lakes 33 b. Resurvey of Sudbury Lake Trout Lakes 34 c. Long Term Monitoring in the Dorset Area 35 d. Smallmouth Bass Reproduction in Acidic Lakes 35 MNR Wildlife Studies The Influence of Lake Acidification on the Reproductive Success of the Common Loon in Ontario 36 C. Remedial Methodologies Development Bowland Lake 36 Shoal Liming 38 ENVIRONMENTAL MANAGEMENT AND ECONOMICS STUDIES A. Damages and Benefits 39 B. Costs of Abatement and Mitigation 39 LABORATORY SUPPORT SERVICES AND METHODOLOGY STUDIES Highlights for 1988/89 43 ABATEMENT 45 TABLE OF CONTENTS (continued) Page COMMUNICATIONS INITIATIVES Ontario 47 United States 47 LEGAL INITIATIVES 49 APPENDIX I International LRTAP Projects - MOE Co-funding 51 International LRTAP Projects - MOE Participation 53 APPENDIX II APIOS Related Technical Reports and Submissions 57 APIOS Related Publications/Papers 73 LIST or FIGURES Page FIGURE 1 1985 502 emissions in Ontario. 3 FIGURE 2 1985 NO^ emissions in Ontario. 3 FIGURE 3 1985 VOC emissions in Ontario. 3 FIGURE 4 1985 Ammonia emissions in Ontario. 4 FIGURE 5 1985 Alkaline dust emissions in Ontario. 4 FIGURE 6 1985 emissions in Ontario of cadmium, manganese, arsenic and iron. 5 FIGURE 7 1971-1987 Ontario total SO2 emission trend (A) and NOx emission trend (B). 6 FIGURE 8 45-day averaged pattern for the tracer PDCH released from St. Cloud, Minnesota during January 5 - February 17, 1987. 7 FIGURE 9 SO2 concentrations in air at Dorset July 17 to August 31, 1988. 9 FIGURE 10 SO4 concentrations in air at Dorset July 17 to August 31, 1988. , 9 FIGURE 11 Measurement of formaldehyde in air at Dorset, August 16, 1988. 9 FIGURE 12 Measurement of hydrogen peroxide in air at Dorset August 16, 1988. 9 FIGURE 13 Dry deposition of lead (1000 kg) into Great Lakes. 10 FIGURE 14 Wet deposition of lead (1000 kg) into Great Lakes. 10 FIGURE 15 Annual SO4 wet deposition in Ontario (average for 1981-1986) 11 FIGURE 16 Annual SO4 dry deposition in Ontario (average for 1981-1986). 11 FIGURE 17 Distribution of copper in surface soils in Ontario. 14 FIGURE 18 Spatial distribution of magnesium in two soil horizons (A and B) at Harp Lake, August, 1982. 15 LIST OF FIGURES (continued) Page FIGURE 19 Limits of accuracy (80% confidence). 16 FIGURE 20 Changes in sugar maple decline indices from 1986 to 1987 for Hardwood Decline Survey plots in Ontario. 18 FIGURE 21 Aluminum in maple foliage from six SO4 deposition zones. 20 FIGURE 22 Location of the study area and regions of high SO2 and NO^ emissions. 27 FIGURE 23 Estimated pH thresholds for extirpation for each of the 13 most common small fish species found in acid sensitive lakes. 35 FIGURE 24 Whole-lake and predicted pH for Bowland Lake, 1982-1988. 37 FIGURE 25 Growth of lake trout in Bowland Lake. 37 FIGURE 26 Egg mortality, 1987/88 over winter. 38 FIGURE 27 Laboratory Workload Summary 44 LIST OF TABLES Page TABLE 1 Annual variation in tree condition assessment at 11 study plots; 1984 to 1988 17 TABLE 2 Summary of the overall average, minimum and maximum levels of nutrients and other elements in the sugar maple and yellow birch foliage samples. 19 TABLE 3 The 13 most common small fish species found in acid-sensitive lakes in Ontario listed by estimated pH threshold for extirpation (disappearance from a specific lake). Suitability as an indicator of early changes in the fish community due to acidification is also given. 34 TABLE 4 VOC Abatement Scenarios - Sarnia & Oshawa-Toronto-Hamilton Metro Areas 40 TABLE b NOx Abatement Scenarios - Sarnia & Oshawa-Toronto-Hamilton Metro Areas 41 TABLE 6 Legal Limits for SO2 for the four Countdown companies 45 TABLE 7 Ontario Hydro's Acid Gas Limits 46 - 1 INTRODUCTION In the mid-seventies results from the Ministry of the Environment Sudbury Environmental Study and Lakeshore Capacity Study clearly demonstrated the importance of long range transport of acid rain precursors and the negative impacts of acidic deposition on the environment. In 1979, the Acidic Precipitation in Ontario Study (APIOS) was launched to further study and document the effects of acid deposition, and to implement an effective abatement strategy. Significant human and financial resources have been committed to this program. The APIOS program has four major components; scientific research, abatement, communications, and litigation. APIOS operates on a 5-year planning cycle and the second five year plan (1986-1990) is nearing the end. This report gives an overview of the mandates of the APIOS program, accomplishments and major findings in FY 1988/89, and future directions during FY 1989/90. Ontario's research and emission control efforts are coordinated with other parts of Canada and the United States since the solution to the long range transport of air pollutants (LRTAP) requires action by all jurisdictions. Appendix I provides a summary of international LRTAP projects with MOE involvement. Appendix II provides a bibliography of APIOS related publications and technical reports. The APIOS program does not have a health effects or materials damage component because these are addressed by small federal specialist groups on a Canada-wide basis. The APIOS Office endeavours to keep abreast of developments in these two areas and ensures that the APIOS technical support is provided when needed (e.g. deposition data). The scientific research component is divided into six working groups and its programs are developed and implemented under the leadership of work group chairpersons. Task 1 Atmospheric Processes Studies Task 2: Aquatic Effects Studies Task 3: Terrestrial Effects Studies Task U: Biogeochemistry Studies Task 5: Environmental Management and Economics Studies Task 6: Laboratory Support Services and Methodology Studies Each program area has its own specific goals and obtains its direction from an interbranch or interministerial working group (the Ministry of Natural Resources contributes to the Terrestrial and Aquatic Effects working groups). In addition, the credibility of the scientific research is assured by a documented and operational quality assurance program. This report will describe the programs in the six scientific work groups and provide background on abatement, communications and litigation initiatives. - 2 - ATMOSPHERIC PROCESSES STUDIES Contact: M. Lusis A. EMISSIONS INVENTORY The compilation of statistics on the production of sulphur dioxide (SO2), nitrogen oxides (NOx) and other pollutants serves several purposes: a. trends in emissions of acid-producing gases are determined and matched with changes in deposition patterns; b. detailed information on SO2 and NOx emissions by geographic location is required by all of the atmospheric models; c. knowledge of the location and magnitude of emission sources is also essential in planning cutbacks of acid gas emissions. The Ontario Acid Rain Emission Inventory was upgraded during FY 1988/89 to provide more complete information regarding SO2, NO^ and VOC (volatile organic compound) emissions as well as related statistics. The 1985 base year Ontario emission inventories for SO2 , NOx and VOC have now been finalized (in cooperation with Environment Canada), and summaries are shown in Figures 1 to 3. A detailed study on some of Ontario's major SO2 emitters was conducted in July and August 1988. Results of this study provide valuable input to long range transport models. Emission inventories for alkaline dust, ammonia and trace metals such as cadmium, arsenic, iron and manganese were also compiled (see Figures 4 , 5 and 6) . Methodology for NO^ and VOC has been upgraded by the use of a model (MOBILE 3) for emissions for mobile sources. Raw data and emissions estimation methods were also established together with Environment Canada for area sources. Trend analysis of the preliminary 1986 and 1987 data shows an ^^% increase in total emissions of 5O2 between 1983-1987. This trend reflects the general economic recovery in the province since 1983. Overall, however, there was a decrease in SO2 emissions from 1980 to 1987 of about 20?6, from 1.8 million tonnes to 1.4 million tonnes. NO^ emissions increased slightly from 1980 to 1987. Vehicles account for about half of the total NOx emissions (Figure 7 ) . MODELLING STUDIES One of the primary goals of the Acid Rain program is to establish source - receptor relationships, i.e., to determine the degree to which a receptor is affected by major emission source areas in North America. Mathematical models combine our knowledge of the movement of air masses and the scavenging and chemical transformation of pollutants during transport into a Transportation Ontario Hydro 23% Others - 17* Algoma (Wawa) - 11% Falcontjndge - 7% Fuel Comb.ilncin NDUSTRIAL Figure 1 . 1985 SO2 emissions in Ontario. Total = 1 ,457 kilotonnes. Olher TransD 16* Trucks-Diesel - 29% Trucks-Gas - 15* Cars-Gas - 56* TOTAL VEHICLES Figure 2. 1985 NO^ emissions in Ontario. Total = 585 kilotonnes. Industrial 14% Fuel Combustion 6% TrucksSCars-Dlesel Cars-Gas 70% VEHICLES TOTAL Figure 3. 1985 VOC emissions in Ontario. Total = 620.7 kilotonnes. ti - Animal Waste Fertiiirer aop 3% Livestock 67« TOTAL ANTHROPOGENIC Figure 4. 1985 ammonia emissions in Ontario. Total = 113.8 kilotonnes. Unpaved Roads 7A% ^ Others 1% Paved Road 3% Industrial 3% Soils 4% Construction Activ. 16% Figure 3. 1985 Alkaline dust emissions in Ontario. Total = 1,572.7 kilotonnes. - 5 - (0 c c |2 z g CO CO UJ lU CO UJ z < o z < 2 0) c c |2 CJ CO (O CO Oi CVi CO I CO z o CO CO lU z o (0 0) c c CVi CD CO z g CO CO UJ 3 Q < 9 1^ (0 o c c i2 (O to CO ■ ni o CO z g CO CO UJ g z UJ CO < Figure 6. 1985 emissions in Ontario of cadmium, manganese, arsenic and - 6 - (A) 3500 ^ 500 71 72 73 74 75 76 77 78 79 YERR 81 8? 83 84 85 (B) 71 72 73 74 75 76 77 78 79 80 81 82 83 84 85 86 87 YERR Figure 7. 1971-1987 Ontario total SO2 emission trend (A) and NO^ emission trend (B). set of numerical equations. Output from the models can be compared to observed deposition patterns, and if the comparison shows a close agreement, we gain confidence that we have a good understanding of the causes and mechanisms involved in acid deposition. Once the models are sufficiently developed, emission reduction scenarios can be assessed by looking at resulting deposition patterns. The models can also be used for the interpretation of data. For instance, because of meteorological variability the deposition of acidic pollutants at a receptor can undergo large fluctuations on an annual basis. This poses a problem in determining the effects of an emission control scenario using the observed data at a receptor. A properly validated model allows us to screen the meteorological variability out so that the expected change in the deposition at a receptor from a given emission control can be evaluated. Several models have been developed and evaluated towards this end. The Acid Deposition and Oxidant Eulerian Model (ADOM) was evaluated for 20 days in April, 1981, coincident with the OSCAR field study (Oxidation and Scavenging Characteristics of April Rain). Several sensitivity tests of the model were also performed. These results were reported in the FY 87/88 annual report. They have since been repeated with a new cloud module. The conclusions have not changed with these new simulations; the predicted and modelled sulphate concentrations in precipitation generally agree within a factor of two. The Eulerian model will be evaluated again in the next two years with data obtained in the joint U.S. and Canada field study project (See Section C below). The study is expected to provide detailed information on many chemical species which the model uses in input and generates as output. The transport module of ADOM has been evaluated against data from ANATEX (Across North America Tracer Experiment). In ANATEX, non- reactive tracers were released at two locations (Minnesota and Montana) and monitored at arcs away from the release points. The spatial resolution of the monitoring network was 3-400 km. Tracer releases took place over a 90-day period in the winter of 1987. Figure 8 shows a long term average (45 days) of the modelled and observed tracer concentrations. The observed pattern is limited by the location and the spatial resolution of the monitors. MM \ / / ^ /\j\ >"7v- 2U0. K. ^^ l? . 3k tUBO • zA 7^^^^. Jc\ te^ IMo' Sy/t ^^Wt ?Ww^ ^ lue. ■A54 ^^y^ ^^\~^^- tiM 1 r^ ^S S^^-„- \u» ^ 7M_ : IjCj J^ *M 1/ ~?;^^ \ \m MB 7XB VUO lUO lUlO lUO tUO tiM 2U0 }IJO MXO ilM Figure 8. 45-day averaged pattern for the tracer PDCH released from St. Cloud, Minnesota during January 5 - February 17, 1987. The solid lines are the modelled pattern while dashed lines show the observed pattern. The units are in femtolitre tracer/litre of air (fl/1) and the values of the contour, starting with the outermost are 0.5, 1.0, 2.0, 5.0, 10.0, 20.0, 50.0 and 100.00. ADOM has also been evaluated for a 9-day, high-ozone episode in June 1983. For this study, a biogenic reactive hydrocarbon emission inventory was developed and added to the input data. Model results were compared with observed hourly ozone concentrations at about 30 stations in Ontario and the northeastern United States. Comparisons of observed and modelled time series indicate that the model is properly simulating both the diurnal pattern and the maximum ozone concentrations. When daily observed maxima at the stations were compared with model results the bias was very small and the geometric standard deviation was 1.4 (i.e., more than 95?o of the predictions were within a factor of two of the observations). This data set was then used to investigate the effects of NO^ and VOC emission reductions on ozone concentrations in Ontario. The conclusions were: Power Research Institute, and the Florida Acidic Deposition Monitoring Program. There was intensive monitoring from July 15 to August 31, 1988 as part of EMEFS. During this time a number of chemical species, including formaldehyde, hydrogen peroxide, ozone, sulphur dioxide and sulphate aerosols were measured at Dorset. Figures 9 and 10 show the six-hour average concentration of sulphur dioxide and sulphate and clearly indicate the pollution episodes (day zero in these plots was July 17, 1988). Some sample results for formaldehyde and hydrogen peroxide levels in air at Dorset, measured by a tunable diode laser absorption spectrometer on August 16, 1988, are shown in Figures 11 and 12. Similar measurements were made at Environment Canada's Egbert and Borden sites, and on board two aircraft flying between the three sites. 1. NOx was the limiting pollutant for ozone production during this episode . 2. Due to outside sources Ontario would be unable to prevent ozone levels exceeding 80 ppb even if Ontario NO^ emissions were eliminated. C. DEPOSITION MONITORING NETWORK The daily and cumulative (28 day) networks were used to monitor deposition in the province through 1988. Data from the daily network forms an important component of the Eulerian Model Evaluation Field Study (EMEFS) which started in June 1988, and is scheduled to run for two years. EMEFS is a cooperative venture between the Ontario Ministry of the Environment, Environment Canada, the US EPA, the Electric Results from the APIOS cumulative monitoring stations located in the Great Lakes Basin were used to assess trace metal deposition to the Great Lakes. Figures 13 and 14 show results for lead. The provincial APIOS network data were also updated with new results, to better determine long-term loadings of acidic substances in Ontario. Figures 15 and 16 show average annual wet and dry sulphate deposition (the dry sulphate deposition includes the contribution from both sulphur-bearing particulate matter and gaseous SO2), based on measurements during the 1981-1986 period. Dorset 6- hour Data ia July to 31 *u9 i9Be Dorset 5- hour Data n July to 11 Aug igas Figure 9. Six hour average concentration of SO2 in air at Dorset, 3uly 17 to August 31, 1988. Figure 10. Six hour average concentration of 5O4 in air at Dorset, July 17 to August 31, 1988, H202 1 ::: i 1 t ••. iM Yi a « • tt ^s a ■ Figure 1 1 . Measurement of formaldehyde in air at Dorset, August 16, 1988. Figure 12. Measurement of hydrogen peroxide in air at Dorset, August 16, 1988. 10 SUPERIOR HURON ^m ONTARIO m MICHIGAN CD ERIE 1982 1983 1984 1985 1986 YEAR Figure 13. Dry deposition of lead (1000 kg) into Great Lakes. ONTARIO MICHIGAN ERIE HURON d] SUPERIOR YEAR Figure 14. Wet deposition of lead (1000 kg) into Great Lakes. 11 - Figure 13. Annual SO4 wet deposition in Ontario (average for 1981-1986). Figure 16. Annual SO4 dry deposition in Ontario (average for 1981-1986). D. OXIDANTS STRATEGY DEVELOPMENT ADOM (the Atmospheric Deposition and Oxidant Model) was used to assess the relative contribution of hydrocarbons and nitrogen oxides to ambient oxidant levels in Ontario. These runs, already referred to in Section B, suggested that control of local nitrogen oxide emissions would be more effective than hydrocarbon emissions control for lowering oxidant levels. Also, most of the oxidant burden in Ontario was attributed to emissions in the United States. A further analysis of the extensive Ontario data during the 1984 Sarnia Oxidant Study confirmed the above conclusions. A draft oxidant control strategy document was prepared, which recommends that (bearing in mind the relatively minor contribution to oxidant levels in Ontario due to local sources, and the substantial costs of control), the provincial government take no additional steps beyond the initiatives already being considered to control oxidant precursor emissions. These initiatives include substantial reductions in hydrocarbons and nitrogen oxide emissions due to revisions in Regulation 308 of the Environmental Protection Act, the adoption of California tailpipe emission standards for light duty vehicles, and a more rigorous vehicle inspection program. The cost of hydrocarbon and nitrogen oxide emission controls for point sources in two industrial areas - Sarnia and the Hamilton-Toronto- Oshawa metropolitan area was assessed, for various control scenarios. The various scenarios and costs are discussed in the Environmental Management and Economics section. E. METEOROLOGICAL STUDIES A meteorological data acquisition system (MDAS), capable of providing support for special studies and episode analysis, as well as modelling activities, has been implemented. MDAS is a computerized system which collects and stores meteorological data supplied by - 12 - Environment Canada from the North American network of weather stations. Air parcel trajectories are also calculated by the system for interpreting event precipitation and other air quality data. During FY 1988/89 meteorological data were acquired and archived on an on-going basis. Air parcel trajectories at various locations in Ontario and eastern North America were calculated and archived on a daily basis. As well, the daily synoptic weather patterns for various locations in Ontario were also categorized and archived. Residence time analyses during transport were also completed. Plans to have a satellite link via the Anikom 100 service to receive the meteorological data from Environment Canada are now actively under development. A meteorological study was published in 1988 concerning the contribution of local and U.S. sources to oxidant levels in southern Ontario. The study found that more than half of the elevated ozone levels in Southern Ontario can be attributed to percursor emissions in the United States. Other data analysis dealt with trends in sulfate and nitrate deposition in the Muskoka area. The decrease in emissions of SO2 in eastern North America in the past decade was strongly correlated with a decrease in bulk deposition rates and concentrations of sulphate and hydrogen ions in precipitation in central Ontario. Nitrate emissions, deposition and concentrations have not changed significantly over the same period. - 13 TERRESTRIAL EFFECTS STUDIES Contact: W. Mcllveen The primary objective of the Terrestrial Effects program is to determine the impact (if any) of acidic precipitation and related pollutants on the terrestrial environment. The program is divided into three sub tasks: Vegetation, Soils, and Forest Productivity and Decline studies (responsibility of the Ministry of the Environment), and the Wildlife sub task (responsibility of the Ministry of Natural Resources). All of these sub tasks include several component projects. A. VEGETATION STUDIES Mobile Rain Exclusion Canopies A fully-automated rain exclusion canopy (REC) located at the MOE Phytotoxicology Laboratory in Brampton is used to assess the impact of acidic deposition and ozone on commercially valuable forest trees. The system consists of three mobile greenhouse shelters which exclude ambient rainfall and apply simulated acid rain (SAR) treatments to test plants established in the field. All aspects of the set-up are controlled by a microcomputer and data acquisition system. Depending on the research objectives, ambient levels of gaseous pollutants (i.e. O3, SO2 and NO^) can be reduced in the field plots via a filtering system and perforated polyethylene distribution tubes. Gaseous pollutants such as ozone can also be injected into the treatment plots. a. Soybean Studies The REC system was used in 1985 and 1986 to investigate the impact of acidic precipitation on yield of soybeans (Glycine max cv . Hodgson). Treatment effects were determined for various components of yield; i.e., seed yield (kg/ha), pod number per plant, seed number per pod, seed weight (g/100 seeds), and plant height. Results of the 1985 field study suggest that increased acid content of SAR had a slight stimulatory effect on soybean yield. For each of five SAR treatments, soybean yield (kg/ha) obtained in 1985 was significantly greater than the 1986 yield. The yield results can be attributed to differences in seed weight caused by environmental conditions specific to the two growing seasons. The acid rain treatments did not produce a yield effect in 1986. b. Forest Tree Species Studies The REC system is presently being used to study the effect of acidic deposition on sugar maples, white spruce and poplar. During the fall of 1985 and spring of 1986, sugar maple transplants from the Dorset area and nursery-grown white spruce seedlings were potted in mineral soil taken from a site near Dorset (the Leslie Frost Centre). The most - 14 - vigorous individuals were used for experimentation under the REC system commencing in the spring of 1987. Rooted cuttings of three clones of hybrid poplar were also planted under the REC system to provide shelter for the maples and serve as an additional species to monitor. The trees were subjected to three different SAR treatments (pH 3.2, 4.3 or 5.6) at regular intervals. Non-destructive measurements on the seedlings include: 1. visible injury rating; 2. photosynthesis rates; 3. throughfall and soil leachate chemistry; 4. plant height, stem diameter, leaf number. Destructive sampling of selected seedlings will be made to investigate: 1 . pigment content of leaf tissues; 2. physical and chemical changes in roots and foliage; 3. mycorrhizae. Results are expected in 1990. Insect - Acidic Precipitation Much of the more severe dieback of sugar maple in Ontario is associated with defoliation by forest tent caterpillars. Since there is a possible interaction of acidic precipitation with insect defoliation (i.e., acid stressed trees may be preferred hosts of the insect), this possibility is being investigated. Potted sugar maples are subjected to simulated acid rain at two pH's. They are then defoliated to different degrees either mechanically or by controlled insect feeding. The trees are monitored for growth and survival. The preference of the insects for foliage subjected to different acid treatments and the growth rates of the insects on these diets is being examined. The first year of the two-year project has been completed. The limited data presently available showed reduced growth of the tree seedlings following both severe mechanical and insect feeding defoliation. Further experimenta- tion is necessary before conclusions on the interaction of the insects with acid treatments can be reported. B. SOIL STUDIES Concentrations of Metals in Surface Soils Surface soil concentrations of nickel, copper, lead, and zinc determined for 300 undisturbed soils across southern and northeastern Ontario (1980-1984) were mapped using the Meteorological Data Acquisition System contour mapping program. The results show that high surface concentrations of nickel and copper centred on Sudbury completely dominate the distribution pattern of these two metals (Figure 17). Figure 17. Distribution of copper in surface soils in Ontario. 15 Surface soil lead concentrations are generally higher in the southern portion of northeastern Ontario than in southern Ontario, but the lead contour maps do not display the degree of dominance of Sudbury evident for copper and nickel. In the northeast, there are two areas where zinc concentrations are high, one north of Elliot Lake, the other near Ranger Lake. These areas are coincident with recent forest fires, and the sampled sites had a predominance of birch and poplar, known accumulators of zinc. Hence these high zinc levels in surface soils in the north may be the result of a combination of forest fire action and biogeochemical cycling by tree species. In the south, high zinc levels exist throughout the soil profile, and are therefore likely a reflection of parent materials. Sources of Variability in Soil Properties This study addresses spatial and temporal variability of soil properties and considers implications for soil baseline monitoring. One site at Harp Lake and another at Plastic Lake near Dorset were sampled on a one metre grid with 33 sample points per site. Samples were collected in the spring, summer, and fall of 1982 and 1983 in order to detect seasonal and yearly variations in 23 soil parameters. Preliminary results show a wide variability in soil properties, with overall coefficients of variation (c.v.) ranging from 95% for dithionite extractable manganese to only 6% for pH. The low variability for pH is clearly a result of its definition because pH is a logarithmic measure of hydrogen ion concentration; the latter property has a c.v. of 56%. Figure 18 shows the extent of spatial variability encountered for exchangeable magnesium across the A horizon (upper surface) and the B horizon (lower surface) of a 10 m grid at Harp Lake. This graph demonstrates the difficulties that are encountered in attempting to quantify a soil property at one site and utilizing this information to determine if there are changes over time. For baseline monitoring studies, it will be necessary to group sites according to both soil sensitivity to acidic inputs and deposition gradients in order to be able to detect any changes. iio r Figure 18. Spatial distribution of magnesium in two soil horizons (A and B) at Harp Lake, August, 1982. Figure 19 is an estimate of the number of sites that would have to be grouped together in order to obtain a given level of accuracy with 80?i confidence for four of the measured parameters (soluble aluminum, clay content, total copper, and pH in water extract). Preliminary results also indicate considerable differences in variability and property means - 16 - LIMITS OF ACCURACY SOX CONnOCNCC 2 J 4 s e n Ai.ES 1011 I2UI4I5I 18 19 2021 22 2324 252627 2829 30 Jl 32 3JJ4 A pMEW Figure 19. Number of sights needed to be grouped together to obtain level of accuracy (80?o confidence). between horizons and emphasize the need for sampling to occur by horizon rather than by depth. Improvement in reducing sample variability could be achieved by pooling samples obtained from a much larger area than can be obtained from a soil pit (i.e. by using a soil corer). Nine of the measured properties showed statistically significant changes in mean values by year. Many of these properties, such as clay content, silt content and organic carbon, would not be expected to show any noticeable change in a short time. The apparent increase in silt content from 1982 to 1983 may be due to an increase in dithionite extractable iron and aluminum and the binding of clay sized particles into silt sized particles. However, no natural physical process could explain the large increase in organic matter content in one year, hence, the yearly changes observed in these properties may be a result of the intensive sampling procedure itself, in conjunction with normal soil forming processes, creating altered conditions in the second year. A dilemma is thus created; if one is to sample intensively enough to properly characterize the spatial variability, there is a possibility that the sampling could affect subsequent measurements and bias estimates of temporal variability. Five parameters showed significant decreases in c.v. from 1982 to 1983. All were metals, and all but one (zinc) exist in more than one valence state. Since 1982 was a very cold and wet year (coldest since 1929), reducing environments would have existed for much longer in 1982 than in 1983. Reduced forms of metals are more mobile than their oxidized counterparts and hence increased variability could be expected in 1982. Detection of these changes over a one year period was unexpected. Nine parameters showed significant seasonal changes. The observed increase in nitrogen content of the A horizon in the fall can be explained as a result of biological activity and leaching from leaf fall. The seasonal decrease in sand content is equivalent to the seasonal increase of silt plus clay. The explanation provided above (changes in dithionite extractable iron and aluminum fractions and larger particle size) is less plausible seasonally than yearly. Although the appropriate pattern of change exists, it is unlikely for 'glueing' materials to be sufficiently strong to hold silt and clay sized particles together as sand sized particles against the forces existing during the analyses. Observed seasonal variations in total copper and nickel concentrations are also not readily explainable. The variability of extractable (pyrophosphate, dithionite, and calcium chloride) forms of aluminum increased in the summer and decreased considerably in the fall. It is of interest that these aluminum measurements, which are of - 17 - primary concern in terrestrial effects studies, are most variable in the season in which they are most likely to be monitored. C. FOREST PRODUCTIVITY AND DECLINE STUDIES deposition, may be responsible for the observed poor tree condition since 1984. Extremes in weather conditions also have a role to play. Defoliation of the trees at some plots occurred in 1987 and 1988 and is anticipated to occur again in 1989. Maple Decline Study This study was initiated in 1984 to determine the role of acidic deposition in the decline of woodlots managed for maple syrup production in the Muskoka/ Haliburton area of Ontario. Permanent observation plots were established to assess tree condition at seven locations. A control site at Thunder Bay was established in an area of low acidic deposition. In 1985, additional plots were added on calcareous soils near Peterborough and in an unmanaged stand in Algonquin Provincial Park. Tree condition has been assessed annually since the plots were established. In general, the trees remained improved slight In 1988, howeve decline in the areas was the h measured (Table reason for the was an increase yellowing of fo attributable to conditions whic and, in some ca of insect defol condition of the the same or possibly ly from 1984 to 1987. r, the degree of two Southern Ontario ighest of any year 1 ) . The primary higher decline index in the degree of liage, partially the drought h prevailed in 1988 ses, to the effects iation. Determining the cause of tree dieback at each site is difficult owing to the many stresses that are or were in effect prior to the dieback. Severe defoliation by forest tent caterpillars in Muskoka in the late 1970's was combined with spring droughts in 1976, 1977 and 1983. Armillaria root rot, tree age, site management and possibly the additional stress of acidic Table 1 : Annual variation in tree condition assessment at the 11 study plots; 1984 to 1988 Mean Decline Index* Plot 1984 1983 1986 1987 1988 Muskoka Mean 22.5 20.9 22.2 18.3 31.2 Peter- borough Mean 16.6 14.2 11.2 17.4 Thunder Bay Mean 18.6 18.4 27.6 15.4 17.3 * Decline index from 0 - 100, ranges are approximation: 0-15 healthy 16-30 moderate greater than 30 severe Hardwood Decline Studies In FY 1985/86 and FY 1986/87, a study was initiated to determine the incidence and severity of hardwood decline across the province. One hundred and ten permanent observation plots dominated by sugar maple were established across the province. Each tree within the plot was assessed according to the amount of dead branches, chlorosis and undersized leaves in the crown. The data was used to calculate a decline index using 0 to represent a tree without any dieback and 100 to represent a dead tree. Data from the original evaluation show plots with moderate to severe dieback in the south-western part of the - 11 province as well as the Niagara and Muskoka areas. Dieback is scattered through the northern part of the study area while there is a broad band of relatively healthy hardwood stands extending from Lake Huron south of Georgian Bay east to the Ottawa area. No pattern of dieback was seen that could be directly related to acidic precipitation patterns; however, soil characteristics, particularly higher buffering potential of limestone- based soils, may have an important role in the distribution of the problem sites. The severity and extent of dieback was greatest where soil was most sensitive and deposition was highest. In 1987, the plots were re-examined to determine whether the condition of the trees as measured by the Decline Index had changed. The 1987 survey identified plots in the regions of Algonquin, Parry Sound, Muskoka, Niagara, London, Cornwall and the north shore of Lake Huron where the Decline Index was higher then in 1986. These areas correspond to known or suspected forest insect infestations. For the majority of the plots not affected by defoliating insects, the mean Decline Index of trees did not change by more than one standard deviation between 1986 and 1987. There was no evidence of a relationship between tree decline and wet sulphate deposition patterns. Changes in decline indices from 1986 to 1987 are shown in Figure 20. Figure 20. Changes in sugar maple decline indices from 1986 to 1987 for Hardwood Decline Survey plots in Ontario. Changes in Decline Index o decrease > 5.4 (1 S.D.) + little change < 1 S.D. • increase > 3.4 (1 S.D.) - 19 - Hardwood Nutrition Studies A potential effect of acidic precipitation is the leaching of plant nutrients from the soil. This could result in reduced plant growth and be reflected in the foliar chemistry of vegetation growing on the site. In 1986 and 1987 foliage and soil chemistry was studied for two tree species; yellow birch (Betula alleqhaniensis) and sugar maple (Acer saccharumT. The intent of the sampling was to identify relationships between foliage and soil chemical properties and to relate these to the condition of the trees at the sites. The results of this study, which included 35 of the Hardwood Decline Study sites for each species across Ontario, indicated that there were no marked nutrient imbalances or deficiencies in the foliage or the soil. A summary of the average mineral element content in the foliage of each species is shown in Table 2. Aluminum which is mobilized following acidification of soil was found to be highest in sugar maple foliage collected at sites within the zone of highest deposition of sulphate in the Province (Figure 21). Table 2: Summary of the overall average, minimum and maximum levels of nutrients and other elements in the sugar maple and yellow birch foliage samples. SUGAR MAPLE YELLOW BIRCH FOLIAGE STANDARD STANDARD ELEMENT MEAN MIN MAX DEVIATION MEAN MIN MAX DEVIATION MACRONUTRIENTS N {%) 1.98 1.42 2.50 0.40 2.55 2.00 3.04 0.35 P (?o) 0.17 0.10 0.31 0.07 0.18 0.11 0.31 0.05 K {%) 0.84 0.58 1.33 0.18 1.13 0.65 1.61 0.31 Ca {%) 1.32 0.72 1.92 0.36 1.40 0.95 2.66 0.42 Mg (?o) 0.19 0.11 0.38 0.07 0.28 0.17 0.41 0.07 S (?o) 0.20 0.15 0.25 0.03 0.14 0.12 0.17 0.02 MACRONUTRIENTS Cu (ppm) 5.4 3.6 7.3 1.3 6.3 4.3 7.9 1.1 Fe (ppm) 84 39 208 79 98 66 208 36 Mn (ppm) 755 82 2280 702 1717 203 5480 1276 Na (ppm) 11.7 10.0 19.0 3.2 14.1 6.0 38.2 7.7 Zn (ppm) 23.0 13.0 48.4 9.8 334.2 100.0 486.0 132.4 OTHER ELEMENTS Al (ppm) 47 20 150 33 54 22 144 33 Cd (ppm) 0.28 0.05 0.52 0.16 2.51 0.56 3.68 1.04 CI {%) 0.06 0.02 0.12 0.03 0.01 0.01 0.06 0.01 Mo (ppm) 0.33 0.25 0.90 0.09 0.48 0.25 0.80 0.08 Ni (ppm) 1.44 . 0.50 6.24 1.22 2.65 1.00 5.76 1.59 Pb (ppm) 1.55 0.50 2.80 1.13 2.26 1.00 4.26 0.88 - 20 - ALUMINUM IN MAPLE FOLIAGE 90 - 80 - ^ 70 - ^ 60 - S 50 - V/ ^ 40 • ! 1 P 1 30 - i 1 % 20 - V/. '/, 10 - n - i i i i i i M i 2^ . ^ 15-20 20-25 25-30 30-35 S04 DEPOSITION RATE ZONE (KG/HaA") Figure 21 . Aluminum in maple foliage sampled from six 5O4 deposition zones. Soil pH was the soil parameter which was most consistently correlated with foliar element concentrations. Foliage of both species contained lower concentrations of calcium and magnesium and higher concentrations of manganese, copper and zinc when associated with lower soil pH. Higher Decline Index ratings were associated with lower soil pH and higher foliar manganese. Further interpretation of the data is warranted and can be used as baseline data for future sampling efforts. The nutritional studies also serve as a basis for mitigative investigations. In a number of locations including Europe and Quebec, considerable resources are expended in an attempt to reverse the progress of tree dieback through the application of plant nutrients or limestone. A great deal of information is required before accurate treatment recommendations can be made about the application of these materials. In 1988, a fertilizer application trial was set up in cooperation with the Ontario Maple Syrup Producers Association. The trial involved four sites, each with trees in two classes of decline (moderate decline and relatively healthy). Treatments included individual nutrients (nitrogen, phosphorus, potassium, calcium, magnesium, lime) and combinations of nutrients in addition to the control. The foliage and soil were sampled prior to treatment to document the nutrient status of each tree. Trees will be monitored to determine if the treatments bring about improved health and nutrient status in future years. Remote Sensing Rapid assessment of the extent and severity of forest dieback relies on techniques with a remote - 21 sensing component. Such techniques are expensive and are still in the developmental stages. In 1988, a relatively inexpensive remote sensing approach was used to study sugar maple dieback. By combing light filters and a series of video cameras it was possible to obtain photographic records of selected maple plots. The video tapes were digitally analysed using a computer. Initially, the method appears to be highly promising but a final report is pending. unpalatable. Cadmium levels in aquatic plants in Algonquin Park, a poorly-buffered acid-sensitive area were significantly higher than those from Cornwall, a well-buffered, acid insensitive site. Moreover, the two species tested that were highly preferred by moose had higher levels of cadmium than did the unpalatable species. D. MNR WILDLIFE STUDIES Cadmium Accumulation by Aquatic Plants Preferred as Forage by Ontario Moose. In Ontario, the highest cadmium levels in the tissues of moose and deer have been found in populations from areas of poorly-buffered and acid sensitive soil. Higher levels have been found in moose than deer. This may be due to the aquatic feeding habits of moose, since many freshwater aquatic plants are known to be highly effective bioaccumulators of metals. Two hypotheses were tested regarding cadmium content in aquatic plants: a. cadmium levels of plants with poorly buffered soil do not differ from levels in areas of well buffered soil; b. species of aquatic plants favoured by moose do not differ in cadmium content from species less favoured by moose. These species of aquatic plants were chosen for sampling according to moose palatability : Utricularia vulgaris, Potamoqeton gramineus, and Nymphaes odorata. The first two are highly palatable while the third is BIOGEOCHEMISTRY STUDIES Contact: P. Dillon 22 A. BIOGEOCHEMICAL STUDY SITES - MONITORING PROGRAMS The biogeochemistry studies provide baseline data about the physical, chemical and biological state of the watersheds. The study results will help to determine the changes that occur over time with continuing acid rain. The APIOS program has established watershed study areas near Dorset (south-central Ontario) and near Thunder Bay (northwestern Ontario). The study catchments located at Plastic and Harp Lakes in south-central Ontario are in a high sulphur deposition area. The Hawkeye Lake site in northwestern Ontario is in a low sulphate loading area. All three sites lie on the Precambrian Shield, the location of most of Ontario's productive forest land. The Shield represents the area most sensitive to acidification and includes prime wilderness and recreational resources. These intensive ' biogeochemical ' studies focus on the chemistry of an entire catchment and emphasize the links between land and water systems. Inputs of rain and snow undergo changes as they pass through the forest canopy, through the forest floor and underlying soil, and finally as they emerge as streamflow discharged from the watershed. The Plastic Lake site has shallow soils with mainly coniferous trees. The Harp Lake site has deeper soils with mainly deciduous trees. The Hawkeye Lake site has soils ranging in depth from very shallow to over 20 m, with a mixed forest stand. Routine sampling occurs at all three sites. Bulk samplers monitor precipitation quantity and quality. Weirs are used to monitor water quantity in the streams draining the study areas, and lysimeters collect the water percolating through the soil . Lysimeter (soil water) data for subcatchments of Plastic and Harp Lakes were used to assess the alkalinity generation in the soils of the two catchments. Plastic soil water had lower alkalinity than that of the Harp soil water because of higher sulphate concentrations. To a typical litre of rainwater percolating through the catchment, upland soils in the Harp Lake catchment add 31 ueq of alkalinity whereas Plastic upland soils add 23 ueq alkalinity. The difference in alkalinity generation is not due to differences in base cation release (138 vs. 139 ueq), but to increased strong acid anion release (143 vs. 82 ueq of sulphate) which - 23 is only partly balanced by increased aluminum dissolution (22 vs. 1 ueq) in the mineral (B) horizons of the Plastic upland soils. Base cations are released from different areas in the soil profile in Harp and Plastic upland soils. In Harp, larger amounts are released in the top organic layer (LFH) causing increased pH and alkalinity there. It is not until the water reaches the lower mineral layers in Plastic upland soils that the base cation levels reach those of Harp. Conversely Plastic LFH layers release larger amounts of organic acids than Harp, however these are almost completely adsorbed in the lower mineral layers of both catchments and there is little resulting differences in the water draining them. Consequently, organic acids have a negligible effect on the differences in alkalinity generation in the upland soils of the two catchments. After water leaves the soil horizons it enters the groundwater pool. The Plastic ground water pool size is very small relative to that of Harp. Consequently there are gross increases in alkalinity in Harp catchment as water passes through the groundwater pool (167 for Harp vs. 5 ueq'L"^ for Plastic). This is primarily the result of base cation release (246 vs. -5 ueq'L"''). The Plastic ground water also loses a small part of its high sulphate and aluminum load. Stemflow (precipitation in contact with tree bark) was monitored at Harp and Plastic watersheds to determine the contribution by stemflow to the flux of ions to the soil/bedrock. This flux was compared to the contribution from incident precipitation and from throughfall (precipitation falling through the forest canopy) . Throughfall concentrations are related to atmospheric sources, canopy composition and dry deposition whereas stemflow is affected by both leaching of ions from the bark and washing off of dry deposits. The forest cover at the Plastic Lake site is dominated by the conifers white pine and eastern hemlock while the forest cover at the Harp Lake site is dominated by deciduous species, soft maple and hard maple. With minor variations due to differences in precipitation frequency and quantity in different years, it was determined that the conifer forest at Plastic Lake intercepted 78?o of the incident precipitation. Most of this, 76?o, was found as throughfall, with only 2?o as stemflow. The Harp Lake forest intercepted B5?d of the incident precipitation, B2?o as throughfall and 3?o as stemflow. Data from February, 1983 to February, 1984, showed incident precipitation pH nearly identical at Plastic and Harp Lake sites, 4.27 and 4.21, respectively. However, upon interaction with the conifer forest, throughfall pH at Plastic Lake was reduced to 4.16, while at Harp Lake the pH increased to 4.33. This effect was even more pronounced in stemflow were the volume weighted average stemflow at Plastic Lake was pH 3.91 , and at Harp Lake was pH 4.59. The neutralizing capability of conifer species is lower than the deciduous species. The dominant anion in all solutions was sulphate. For the period discussed above, sulphate concentrations in incident precipitation at Plastic and Harp Lake sites were 54 and 61 ueq-L"^, respectively. Throughfall enrichment of sulphate at Plastic Lake resulted in a concentration of 103 ueq*L~', while at Harp Lake this enrichment increased sulphate to 24 80 ueq'L"''. Stemflow enrichment resulted in sulphate concentrations of 260 and 200 ueq-L"'' at Plastic and Harp Lake, respectively. These differences may be due to the superior ability of conifers to intercept dry atmospheric sulphur compounds, as well as the presence of needles during the entire year. The contribution of dry deposition is presented in an analysis of sulphate in precipitation events following dry weather of between 24 and 48 hours in duration and dry weather of greater than 120 hours in duration. Average throughfall concentrations at Plastic Lake were 100 and 120 ueq-L"'' , for the two durations respectively. The base cations calcium, magnesium and potassium were all markedly enriched in throughfall and even more so in stemflow. Sodium concentrations were only marginally enriched in throughfall and stemflow. Enhanced enrichment in base cations was observed in the spring and fall when cuticles were not fully developed or when foliage senescence permitted accelerated leaching of these bases. Ammonium ions were marginally reduced in throughfall, but substantially reduced in stemflow. Nitrate was marginally enriched in throughfall under both forest types, but remained unchanged in stemflow at Harp Lake and greatly reduced in stemflow at Plastic Lake. Nitrogen compounds are conserved in the canopy and assimilated by the foliage or microflora on the tree. While the volume of stemflow was small when compared to throughfall, the concentrations of most ions in stemflow was very high. The bulk of this enrichment is due to leaching from the bark of the trees. In stemflow, high loading of ions including hydrogen, occurs in a small area around the tree. This effects the properties of soil near the tree and the soil water composition. B. PROCESS STUDIES Bioaccumulation of Nutrients Estimates of the standing crop and growth rates of all major tree species have been made in the upland forest ecosystem of the Harp and Plastic sites. These will be used to calculate the annual increment of base cations, nitrogen and sulphur. Researchers will use these data to calculate the rate of proton production as a consequence of forest growth as well as the rate of base cation loss from soils. Comparisons of standing crop measurements will be made between stands, and with other forest stands in different deposition zones. These estimates will be integrated with known nutrient requirements of major tree species and with soil content and availability of these nutrients. The study results will ascertain the adequacy of current rates of nutrient uptake for maintaining normal forest productivity and possible effects of acid deposition on these rates. Results are expected in the fall of 1989. Mineral Weathering Rates The purpose of this study is to identify the important weathering reactions that occur within a catchment and estimate the whole catchment rate of these reactions. Plastic Lake catchment was selected as the primary study area. The two dominant rock types in the catchment are granitic gnesis and amphibolite. The soils are made of quartz, plagioclase, K-feldspar and vermiculite. 25 The time-integrated rates of removal of the important bulk chemical constituents since the time of glaciation have been determined from the soils of the Plastic Lake watershed. The relative rate of removal of these constituents in kg/ha/yr decreases in the order silica > aluminum > sodium > potassium > calcium > iron > magnesium. The essential mineralogy of the soils of the Plastic Lake watershed includes quartz (30?o), plagioclase feldspar (30%), potassium feldspar (15?0, vermiculite iM%) , amphibole {^0%) , and goethite (3?o). The rates of removal of the various chemical constituents have been recast into the essential mineralogy to determine mineralogical weathering rates. Plagioclase feldspar is the most important mineral neutralizing acid within the soils through mineral dissolution. This mineral accounts for 55?o of the acid consumed and feldspars as a whole consume 15% of the total. The estimated dissolution rate of albite within the soils (1.75 * 10-12 mol (Si)/m2/sec) is approximately one order of magnitude less than experimentally derived rates. The estimated present day chemical weathering rate for the Plastic Lake watershed is approximately 250Sd greater than that of the long-term rate. This 2.5-fold increase may be a result of the input of anthropogenic acids into the Plastic Lake watershed. Another study was conducted to assess the relative importance of inorganic (hydrogen chloride, hydrogen fluoride) and organic (oxalic) acids to feldspar mineral weathering. After leaching minerals for approximately 72 days, the mineral surfaces were analysed using SIMS (Secondary Ion Mass Spectrometry). Both the hydrogen fluoride solution and the oxalic acid solution were shown to be strong complexers of aluminum. When other minerals such as Bytownite (a more calcite plagioclase) were used, it was shown that the nature of the mineral itself was important in the way in which the species dissolved. In another study, samples were collected from Plastic Lake and slices were taken from stones in the till. Depth profiles were made from naturally weathered feldspars and from exposed fresh feldspars as a control. For weathered plagioclase, the surfaces are highly aluminous and contain large proportions of calcium which means that the plagioclase is amorphous and susceptible to cation exchange on the surface. For vermiculite compositions, significant absorption/exchange of calcium is suggested at the surface. Vermiculite and plagioclase make up 70 to 75?o of all materials at Plastic Lake. These substances probably have an effect on the chemistry of the runoff of the Plastic Lake catchment. The mineral weathering information will ultimately be incorporated in the models of long-term changes in stream chemistry to determine the rate of acidification in the aquatic systems in the Muskoka-Haliburton area. Sulphur Adsorption Studies Sulphate is important in terms of watershed acidification and many factors influence its adsorption and retention. - 26 - Soil samples were taken from Plastic Lake subcatchment 1 from the B horizon. Soils from this region are typically acidic podzols. Results of the laboratory studies show that higher in the soil horizon, there is a larger proportion of adsorbed sulphate than lower in the horizon. For these upper regions, a decrease in acid loading could result in the soil being an additional source of sulphate. With increased deposition, additional adsorption is possible. These results are being used in a catchment sulphate adsorption model. Groundwater Studies Groundwater was surveyed at one of the catchments of Harp Lake. A groundwater monitoring network consisting of water table wells and piezometers was installed in order to collect hydrologic and chemical information. Results demonstrate that the dominant geochemical process in the groundwater in this watershed is silicate weathering and that alkalinity generation occurs along with silicate weathering in the deep basal till. AQUATIC EFFECTS STUDIES Contact: W. Keller - 27 A. CHEMICAL STUDIES Calibrated Watersheds a. Chemical Limnology The Limnology Section Resources Branch has monitored a set of 20 lakes in the Muskoka (Figure 22). Data co cover periods of 7 to Researchers use these measure the long-term acid deposition and t inputs on the chemist of the study lakes. of the Water intensively streams and 8 Haliburton area llected now 13 years. data to effects of race metal ry and biology Figure 22. Location of the study area and regions (shaded) of high SO2 and NOj( emissions. In the past few years, the relative contribution of nitric acid to precipitation acidity in eastern Canada has increased. As a result, researchers have become concerned about the potential deleterious effects of nitrate deposition on terrestrial and aquatic ecosystems. To gauge the extent of this impact, annual mass balances for nitrates and ammonium were calculated for several forested catchments and lakes in Ontario. The analysis of nitrogen retention suggests that nitrogen saturation of lakes and watersheds has not occurred at present nitrogen loadings in eastern Canada, although there may be exceptions in specific stream catchments. Increased nitrate deposition will result, however, in higher concentrations of nitrate and greater acidity in stream and lake waters, while decreased deposition should result in increased alkalinities. Another study analysed alkalinity decreases during snowmelt in 1984-86 for 15 headwater streams and lake outflows in three central Ontario catchments. These depressions were likely to be dominated by sulphate increases as the degree of stream acidification increased. Neither nitrate nor organic acid anions were significant contributors to alkalinity depressions. 28 The data collected from these studies will be used to determine target loadings for nitrogen and to refine the existing target for sulphur deposition. b. Metal Contaminants Surveys of contaminant levels in Ontario fish have shown widespread mercury contamination even in areas remote from local anthropogenic sources. Also, there appears to be a tendency for mercury levels in acidified lakes to exceed those in non-acidified lakes. Currently, the source of this contamination is unknown. However, the widescale nature of the contamination suggests either geologic release of mercury to lakes is common or the atmosphere is dispersing and depositing mercury over much of the continent. Studies are under way to identify the sources of mercury in sensitive areas and to determine the relationships between mercury concentrations in water and levels in biota. Mercury in precipitation and in the major streams of a central Ontario lake (Harp Lake) has been measured over the past year. By coupling these measurements with precipitation depth and stream discharge information, scientists have estimated the amount of mercury supplied to the lake by streams and by precipitation. The study showed that volume weighted mercury concentration of precipitation was 10.2 ng'L"'' and was 3 to 6 times higher than streams. Direct wet deposition accounted for over half of the supply of mercury to the lake. Watersheds retained most of the mercury deposited on them. This study implicates the atmosphere as the principal source of mercury to Ontario lakes and probably to the fish in those lakes. As a result, control and reduction of mercury emissions to the atmosphere must be addressed. The anthropogenic acidity of atmospheric deposition has increased the export of aluminum, manganese and possibly trace metals (lead, copper, cadmium, zinc) from acidified catchments. A recent study documented the deposition of trace metals onto the Plastic Lake catchment and determined where in the catchment they were being transported . Results showed that precipitation in the Muskoka-Haliburton area contained trace metals (median values were 0.08, 2.28, 1.1 and 3.7 ug'L"'' for cadmium, lead, copper and zinc respectively). A review of the concentration of these metals at various points in the watershed shows increased exports of cadmium and zinc from the mineral horizons of soils impacted by acidic deposition. Conversely, lead and copper were not exported from the upland soils. c. Extensive Lakes Sampling During 1988-89, several regional lake surveys were completed. The Northeastern Region continued to monitor a large set of lakes to determine whether lake water chemistry in the Sudbury area has continued to respond to reduced emissions from the Inco and Falconbridge smelters. The Northwestern Region surveyed over 100 lakes north of Ignace. The purpose of this survey was to fill in a large geographic area where little or no lake water chemistry data existed previously. The Southeastern Region surveyed smaller lakes in the region to fill a gap in the database. Smaller lakes had not been adeguately sampled, and many lakes were missing complete water chemistry. 29 Dorset research centre surveyed 150 "ultra-sensitive" lakes (alkalinity less than 35 ueq'L"'') which had been sampled in 1982 and 1983. The purpose of the survey was to determine whether there had been any detectable change in pH or alkalinity in low alkalinity lakes in central Ontario. Missing watershed and lake area data for well over 1000 lakes were determined by digitizing topographic maps. These data will be used to estimate the number of lakes in each watershed in various acid sensitivity categories for estimations of the lake resources at risk. The data base for Ontario now consists of partial chemical data of 6000 lakes, and relatively complete information on over 3300 lakes. In the southern and central parts of the province, this constitutes a significant proportion of the overall lake population. The water chemistry in large areas of Northern Ontario remains unknown. However, these areas of the province receive little in the way of acid deposition, and although many of those lakes may have low acid neutralizing capacity, they are not in danger of acidification unless there are drastic increases in sulphur emissions. A complete assessment and documentation of the data base (pH, alkalinity, variety of nutrients and some metals) is in preparation, and will provide an extensive synoptic look at the spatial patterns of water chemistry within the province. B. BIOLOGICAL STUDIES Lake pH - Algal Sediment Fossils The "new" diatom taxonomy published recently by the U.S. based paleolimnology group PIRLA was applied to the 50 lake calibration set from Ontario. Some sections of cores from Hannah Lake and Clearwater Lake (Sudbury area) have been analysed as a test of the diatom calibration. A first draft of the ch scale calibration (same was also prepared. Cor Plastic and Clear Lakes Twp.) were analysed so down-core histories of lakes (Plastic, Clear, Pincher, Lady, Raven) a for both the diatom and scale calibration. rysophyte 50 lake set) es from (Sherbourne that the same six Maggie, re available chrysophyte A third calibration was developed using chrysophyte cysts. About 130 different cyst morphotypes were used to develop calibration equations (r^ greater than 0.9) on the same 50 lake set. Analyses of cysts in core sections from Plastic, Maggie and Lady have begun. The inferred pH history of these lakes will be available by all three techniques (diatoms, chrysophyte scales and chrysophyte cysts) by 1990. Filamentous Algae Spatial and temporal analysis of benthic algal populations in Swan Lake (Sudbury area) was used to determine changes in algal growth due to pH changes since 1981-82. There was a decrease in algal abundance in 1987 as pH increased, and an increase in abundance in 1988 as pH decreased. The seventh consecutive year of algal mapping was completed in Bowland Lake (whole-lake neutralization study), and Lake 502S (whole-lake acidification study). Increased growth of algae in Bowland Lake (which is now reacidifying) , and Lake 302S, is also consistent with acidifying systems. Filamentous algae in Plastic Lake were mapped for the eighth consecutive year. These data are used to evaluate seasonal and year - 30 to year changes in algal growth. Plastic Lake also serves as a valuable reference to assist in the interpretation of algal growth on less intensively studied lakes. Aerial mapping of Lake of Bays was continued for the third consecutive year. Results showed that about 4 to 10?o of the shoreline (mostly in the smaller bays) was covered with filamentous algal clouds during 1986-88. This may be an indication of early acidification stress. Follow-up statistical analyses to the 1986 Cottager Questionnaire Survey related lake physical/ chemical characteristics to predicted algal status. Lake pH was one of several statistically significant variables that explained algal presence. A final report was received on the taxonomy of Zygnemataceae in Ontario lakes. Results show an apparent pH preference associated with various species of filamentous algae. Zooplankton Several studies are underway to determine the effects of acidification on zooplankton in Precambrian Shield lakes. To aid in understanding the mechanisms of the decline in richness and alterations in the structure of the zooplankton community of Plastic Lake, short term intensive studies were initiated. Studies included the impacts on zooplankton of predation by larval Chaoborus and fish, parasitism by microsporidia, and inter-and intra-specific competition. The impact of acidification on Daphnia galeata mendotae Birge, a very common large cladoceran herbivore in lakes of eastern North America was investigated. Results from laboratory toxicity studies, in soft waters, demonstrated that this zooplankton species is highly acid sensitive. Observed distributions in 445 dilute Ontario lakes subjected to differing degrees of sulphur deposition and spanning a wide pH gradient, are consistent with laboratory studies, showing a substantial decline in the abundance of D.q. mendotae near pH 6.0. The close agreement between field and laboratory data indicate that widespread negative impacts on this important species have occurred due to acidification. Investigations of the impacts of acidification on littoral microcrustacean communities have been initiated in collaboration with staff of the National Museum in Ottawa. Temporal patterns in the species richness of crustacean zooplankton communities were assessed in eight Sudbury area lakes, based on data collected between 1973 and 1986. During this period, the study lakes showed general reductions in acidity and trace metal concentrations related to reduced contaminant emissions from the Sudbury smelters. Despite water quality improvements, several of the study lakes continue to have low pH (less than 5.5) and elevated trace metal concentrations which have inhibited recovery of zooplankton diversity. However, in lakes with current pH near 6.0 and low trace metal concentrations, substantial increases in average crustacean species richness have occurred. Invertebrates Scientists are comparing stream insect data collected 50 years ago from surveys of two low-alkalinity streams in Algonquin Provincial Park with data collected from recent surveys (1984-1986). The same species were observed in 1984-86 as were observed 50 years ago in streams where pH shifts were small (6.4 to 5.7). But, at sites 31 where large pH decreases occur (6.4 to 4.9), many mayfly and stonefly species present 50 years ago had disappeared by 1984-86. We know that these insect species are sensitive to low pH. This loss of acid-sensitive species shows that poorly buffered surface waters have acidified somewhat over the past 50 years. The effects of short-term pH depressions in spring on whole-body concentrations of nine metal cations (calcium, magnesium, sodium, zinc, lead, aluminum, manganese, cadmium and iron) and survival of two species (one mayfly species and one blackfly species) of aquatic insects collected from two habitats with year-round differences in pH were examined in a transplant experiment. Survival was close to 100?o in 4 and 10 day in situ toxicity tests prior to and during snowmelt at pH levels ranging from 6.5 to 4.2. Both species transplanted from pH 6.2 to 4.2 streamwater had significant decreases in whole-body concentrations of calcium, aluminum and manganese. Additionally, mayflies had significant losses of magnesium, iron and lead, while blackflies decreased in whole-body sodium and zinc concentrations at the low pH (4.2). The percent of aluminum adsorbed doubled in transplanted (versus control) mayflies, but the overall whole-body aluminum concentration decreased. Trends in the data support the hypothesis that adsorption of aluminum increases at lower pH levels. Toxicity Testing The absence of a species from a lake with low pH waters or even the observation of a population failure in an acidifying lake does not constitute proof that a species is adversely affected by acids. To establish a cause-effect relationship between an acid and the loss of a species, controlled laboratory toxicity studies must be conducted. These data along with population data provide evidence of the acid tolerance of a species. Such studies may also provide information on the relative sensitivity of different species to acids, and they can be used to investigate the influence of other water quality factors on the sensitivity of biota to acids. In the past, the emphasis in toxicity testing has been on sport fish, but survey data suggest that many of the small forage fish, in particular the cyprinids, are the most acid sensitive group of fish. Consequently, recent toxicity work has focused on forage fish. In 1988 creek chub, blacknose dace. Northern red belly dace, golden shiner, bluntnose minnow and fathead minnow at the embryo-larval stage (the most sensitive life stages) were tested for their acid sensitivity. Bluntnose minnow and creek chub were most sensitive with a 20 day LC50 of about pH 5.6. Golden shiners were most resistant, with a 20 day LC50 of about pH 4.6. Fathead minnow, blacknose dace and northern redbelly dace were intermediate in sensitivity. Essentially all of the mortality occurred during the embryo stage, and most of this in the first few days of exposure. Times to hatch were delayed slightly, but only near the LC50. Similar work will be conducted in 1989 in order to fill in some gaps in the 1988 data, and to extend the data set to include common shiner, rainbow smelt, and sculpins. Ultimately these data will be compared to survey data on the same species. Acids exert their toxic effects by disrupting ion regulation, and it is known that high levels of metabolic ions (calcium, magnesium and sodium) in the water can reduce acid toxicity. However, there is little - 32 - work over the natural range of these ions in softwater lakes. Their significance for the survival of fishes subjected to acid stress is not clear, nevertheless, there are some indications that acids may be much more toxic in the most dilute waters of Precambrian Shield lakes compared with waters of higher ionic content. To determine whether the ionic composition of lakes is a factor, the effect of varying calcium and sodium concentrations on the toxicity of acid to fathead minnows has been studied. Using specific ion concentrations, the results show that calcium and sodium decreased the toxicity of acid solutions anywhere between 0.1 and 0.4 pH units. More dilute combinations of calcium and sodium must still be tested. Biological Survey Historically, research has concentrated on the adverse effects of acidification on sport fish. Recently, the emphasis has shifted to more sensitive organisms, the benthic invertebrates. They form an important part of the diet for sport fish. Biological surveys of softwater Shield lakes were designed to identify aquatic invertebrates that may be sensitive to low pH and to quantify their response to low pH. Sampling of the littoral zone (shoreline) invertebrate community was completed on approximately 60 lakes during the fall of 1987. Concurrent water samples were taken for chemical analysis. Additional samples were collected in the fall of 1988 to augment the data on low alkalinity lakes. The biological samples are being processed to identify species to the lowest practical taxon. Statistical analyses of the chemical and biological data will determine any significant relationships between the chemical parameters and the occurrence of particular biota. A report on this study will be available by the end of Fiscal Year 1989/90. Biological Monitoring The decline of a population of plants or animals in response to deterioration of water quality due to acidification is highly variable. It may be slow and barely perceptible over a span of a few years or it may be quite abrupt. The rate of population decline appears to be related to the normal lifespan of the species. Because adult organisms tend to be more tolerant than young or newborn animals, long lived animals may persist years after they fail to reproduce. The persistence of adults and occasional successful recruitment prevents abrupt population failure. Many aquatic animals, however, live only one or two years and only breed once in their life. Because of these life cycle characteristics their populations can decline rapidly after recruitment failure, and in several instances local extinctions of snails and amphipods have been documented in acidifying lakes in the Muskoka-Haliburton area. In 1988 the Biological Studies Unit of the Dorset Research Centre initiated a monitoring programme that focuses on short lived species. Although species with short life spans can be found within all major groups of animals, the greatest concentration of them is found among the benthos, the organisms living on the bottom of a lake amid the rocks, plants, and mud, and it is toward this group that the programme is directed. The initial work emphasized evaluation of methods (spring vs. fall sampling, determination of the optimum number and location of traps - 33 - for crayfish) and site documentation (aerial photography). These data are currently under analysis, but some of the preliminary results are quite interesting. Of the twelve lakes sampled, four of them contained Orconectes virilis , a species of crayfish which is known to be sensitive to acid conditions. The four lakes spanned a range of pH from slightly acid to circumneutral (around pH 6.5), and over this range there was a clear correlation of shell hardness with pH. Moreover, the animals caught in the most acid lake were all large adults; no young animals were caught. That is, it appears that crayfish in this lake are the remnants of a population on the verge of local extinction. Future results from this lake will be most interesting. Cursory examination of other littoral benthic show that there is a hu between the number of o caught by the "kick and sampling method in the fall. It appears that have at least 10 times of organisms as the spr and clearly the fall is time to sample. the data for organisms ge difference rganisms sweep" spring and fall samples the numbers ing samples, the best Similar monitoring activities were initiated by the Department of Fisheries and Oceans in other areas of Canada. The data from south-central Ontario will be integrated with the national database to examine regional and temporal trends in community composition. Metal and Organic Residue Monitoring a. Monitoring Mercury Levels in Yearling Yellow Perch This program is in its eleventh year for lakes in Muskoka-Haliburton with fewer years of data in the Sudbury, Chapleau and Thunder Bay areas. Using data collected over the period 1978-87, pH explained 64?o of the variability in mercury in yearling yellow perch in 15 lakes in Muskoka-Haliburton. There were no trends in mercury levels in the perch over the ten year period (1978-1987) in any of the lakes. b. Investigating Relationships Between Mercury in Sport Fish and Lakewater Quality Data collected under the Contaminants in Sport Fish Program and the Acid Sensitivity Program were used to assess the relationship between lake water quality and mercury in sport fish. The focus to date has been on lake trout and smallmouth bass. These results were reported in the 1987/88 APIOS Annual Program Report. Similar analyses are currently underway for walleye, pike and brook trout. MNR Fish Studies a. Occurrence of Cyprinids and Other Small Fish Species in Relation to pH in Ontario Lakes. Data from 426 Ontario lakes were used to determine how fish species number was empirically related to lake area and pH. In lakes with pH greater than or equal to 6.0, the total number of species increased with lake area, whereas the number of cyprinid species was generally unrelated to lake size. Accordingly, the fraction of total species number comprised of cyprinid species decreased with increasing lake size. Taking the effects of lake size into account, total number of species, total number of cyprinid species, and cyprinid fraction decreased with pH below pH 6.0. An augmented set of 488 lakes was used to evaluate the potential of the 13 most common small fish species as early indicators of 34 - changes in the fish community due to acidification. The most promising species were: fathead minnow (Pimephales promelas) , common shiner (Notropis cornutus), bluntnose minnow (Pimephales notatus) , blacknose shiner (.Notropis heterolepis) , and slimy sculpin (Cottus coqnatus) (Table 3, Figure 23) . b . Resurvey of Sudbury Lake Trout Lakes A chemical survey was conducted in January 1987 to resample 106 lake trout lakes that were originally sampled in January 1980. Similar methods were used to collect for determination of pH, alkalinity and specific conductance. Substantial improvements were detected. The number of lakes classified as acid stressed (pH less than 5.5) dropped from 46 (43.2?o) to 20 (18.9?0 in 1987. Biological resurveying began in 1988 to examine changes in the fish communities in lakes with improved water quality. Twelve lakes have been resurveyed (initial surveys: 1982-1985) to date. An additional 24 lakes will be resurveyed in 1989. Table 3: The 13 most common small fish species found in acid-sensitive lakes in Ontario listed by estimated pH threshold for extirpation (disappearance from a specific lake). Suitability as an indicator of early changes in the fish community due to acidification is also given. pH Thres- hold for Species Extirpation Slimy Sculpin 5.8 - 6.4 FAIR Blacknose Shiner 5.8 FAIR Fathead Minnow 5.5 - 5.8 GOOD Common Shiner 5.4 - 5.8 GOOD Bluntnose Minnow 5.6 FAIR Iowa Darter 5.4 FAIR Finescale Dace 5.4 POOR Brook Stickleback 5.1 - 5.3 POOR Creek Chub 5.0 - 5.2 POOR Pearl Dace 4.7 - 5.2 POOR Lake Chub 4.7 - 5.1 POOR Northern Redbelly Dace 5.0 POOR Golden Shiner 4.7 - 4.9 POOR Suitability as Indicator Species Restricted to Northwestern Ontario Low Occurrence Restricted to South-central Ontario Restricted to South-central Ontario Restricted to South-central Ontario Possible Increase in Abundance Possible Increase in Abundance 35 - SPECIES Slimy sculpln Blacknose shiner Fathead minnow Common shiner Bluntnose minnow Iowa darter Finescale dace Brook stickleback Creek chub Pearl dace Lake chub N. radbelly dace Golden shiner 4.5 5.5 PH 6.5 Figure 23. Estimated pH thresholds for extirpation for each of the 13 most common small fish species found in acid sensitive lakes. Ranges are shown when specific pH values could not be determined. c. Long Term Monitoring in the Dorset Area The trend-through-time monitoring program was amalgamated with the Muskoka Assessment Unit in Bracebridge. The baseline surveys that began in 1982 were completed on the original 12 lakes in 1988. Baseline studies on the additional "ultra-sensitive" lakes will be completed in 1989. Staff are now concentrating their efforts on data analysis and reporting. The results of these analyses will be used to design and schedule the next round of monitoring. Results will be available next year. d. Smallmouth Bass Reproduction in Acidic Lakes The effects of water quality in five acidic lakes on overwintering young-of-the-year and introduced adult smallmouth bass (Micropterus dolomieui) were determined in two separate experiments. Young-of- the-year (YOY) were held through the winter (November-April) in five lakes (mean winter pH 4.8 - 5.9) in the La Cloche Mountain area of Ontario. Survival declined with decreasing pH and increasing dissolved metal concentrations. Overwinter survival was 0% for YOY in Acid, Partridge and Terry lakes (pH 4.8 - 5.5: total aluminum 0.010 - 0.252 mg'L-''), but varied markedly (0 to 100?i) in George (pH 5.8 - 5.9: total aluminum 0.050 - 0.062 mg-L-'') and A.Y. Jackson lakes (pH 5.8 - 5.9; total aluminum 0.028 - 0.041 mg-L"'') Wild adult bass from a number of circumneutral lakes in the Killarny area were transferred to four of the same lakes (A.Y. Jackson, Terry, Partridge, Acid) that were used in the YOY experiment. Survival estimates were obtained from snorkelling surveys during two spawning seasons (1987 and 1988). Adult survival was at least 55?o (1987 and 1988) in A.Y. Jackson Lake (pH 6.1), at least ^2.b% (1987) and ^.2% (1988) in Terry Lake (pH 5.3), and zero in Partridge (pH 5.1) and Acid (pH 4.8) lakes. Spawning was observed only in A.Y. Jackson Lake and subsequent survival of the early life stages was related to lake chemical conditions. A.Y. Jackson (pH range 5.7 - 6.4; total aluminum range 0.028 - 0.100 mg-L"'') was the only lake, of the five studied, with ambient water quality currently suitable for supporting a self-sustaining smallmouth bass population. - 36 - MNR Wildlife Studies The Influence of Lake Acidification on the Reproductive Success of the Common Loon in Ontario This is a joint project with the Long Point Bird Observatory. The objectives of this study were to: 1 ) examine the mechanisms responsible for the effect of acidity on the reproductive success of the Common Loon and 2) identify how Common Loon reproductive performance and behaviour can be used to assess lake acidity. A pilot project provided behavioral observations and prey sampling on 6 of 32 lakes originally surveyed in the Muskoka-Haliburton area of Ontario in 1988. Success rating of foraging dives appeared to be related to the type of prey utilized. In general, loons feeding their young primarily invertebrates had a success rate higher than that of loons on lakes where chicks were fed primarily fish. Recommendations for further study include: an increased number of lakes to be surveyed observations throughout the breeding season (May to September) and increased prey sampling. The Wildlife Toxicology Fund has recently approved funding for continuation of this study for 3 years, from 1989-90 to 1991-1992. C. REMEDIAL METHODOLOGIES DEVELOPMENT Bowland Lake The lake was limed in 1983 with 84 tonnes of dry calcite. After liming the pH rose from 5 to 6.7, alkalinity increased from 0.3 to 4.5 mg-L"^ and total aluminum dropped from greater than 130 to 30 ug'L"''. Models predicting lake reacidif ication have been compared to actual water chemistry in the six years since liming (Figure 24). Whole lake integrated samples for pH show higher than predicted values in later years, probably due to high algal production . Lake trout stocked after liming are reproducing successfully, as three year old recruits have been captured. Lake trout growth is comparable to other lakes in the region. A perch population which had remained in the acidic lake, first increased following liming, then declined in numbers as competition and predation from lake trout increased with growth of the stocked trout (Figure 25). Lake trout eggs initially survived well in bioassays conducted on the near shore shoals after liming. In 1986 and 1988 however, survival declined in response to declining water guality during spring run-off and decreased whole lake buffering protection. Benthic invertebrates exhibited shifts in biomass distribution among the major taxa in 1988 with Chaoborus almost disappearing from the hypolimnion. Crayfish numbers declined in 1988 although the incidence of softshell remained low. 37 Figure 24. Whole-lake and predicted pH for Bowland Lake, 1982-1988. 500 400 300 200 100 1982 Coh 1983 Coh 0 ^-' ' ^ 83F 84F 85F 86F 87F 88F COLLECTION PERIOD Hills L. ond N. Boy 1982 cohorts grouped together. Spring ond Fall Periods Figure 23. Growth of lake trout in Bowland Lake. 38 In contrast, littoral and planktonic invertebrates showed dramatic increases in abundance in 1988. These changes may be attributable to changes in predation pressures. Prior to neutralization, greens and blue-greens dominated the phytoplankton community. In the last two years, there has been a decrease in the diatoms which increased after neutralization, with a subsequent increase in blue-greens possibly in response to changes in water chemistry. Shoal Liming Pilot scale shoals (3m x 6m) were built with gabion size calcite rubble in George and Johnnie Lakes in Killarney Provincial Park. Results from egg incubation experiments on these and Laundrie Lake (studied in 1985-87) show that calcite treated shoals definitely improve survival of lake trout eggs when mortality due to acidification is high (Figure 26) . Shoal liming is only useful, however, when whole lake water chemistry is of sufficient quality to allow the fry emerging from the protection of the shoals to grow into adult fish. This may be in a marginally acidic lake or in a neutralized lake both of which may require protection for lake trout embryos from acidic spring run-off. Psrcem MortaJiiy J hnnie , George L "1 tuifffcr" 1-C 1-T 2-C 2-T 1-C t-T 1-C 2-T Stage at Death WM Pr*-0yM ^S Byea dD Httcnaa C • C««trel T • Ttvttmtnt Figure 26. Egg mortality, 1987/88 over winter. 39 ENVIRONMENTAL MANAGEMENT AND ECONOMICS STUDIES Contact: 3. Donnan A. DAMAGES AND BENEFITS The focus of this work has been on ozone. Staff in Policy and Planning Branch and Air Resources Branch collaborated to generate estimates of the potential economic benefits to crop production of reducing ambient ozone concentrations. Health and materials effects were also examined. 8. COSTS or ABATEMENT AND MITIGATION Three investigations on the control of precursors to acid deposition and ozone formation were completed: 1 • "Countdown Acid Rain: Future Abatement Strategies". 2. "Nitrogen Oxide and Volatile Organic Compounds Abatement Cost Study". 3. "Cost Effectiveness of Mobile-Source Pollution Control System". 901 ,000 tonnes per year for SO2 and 578,000 tonnes for NO^ as NO2. Costs of emissions control from the sources were estimated for further reductions of 10, 30 and 50 percent beyond this status quo scenario. The official SO2 emission target for 1994 is 885,000 tonnes, or 16,000 tonnes below the "status quo" scenario used in the report. In practice, this difference will be absorbed by a combination of the four major sources emitting at a rate below their legal limits together with changes in emissions from other sources. In addition, the magnitude and costs of abatement in other industrial sectors which would have to be made if one or two of the major sources were unable to implement their mandated reductions were also produced. The numbers are intended to be indicative only, since they are based on a number of assumptions including the cost of types of abatement equipment chosen as surrogates for what might actually be used. The first study defined and evaluated options for further reductions in SO2 and NO^ emissions assuming that Inco, Falconbridge, Ontario Hydro and the Algoma Steel iron sintering operation in Wawa are operating at their 1994 legal emission limits. Other sources are assumed to emit at their 1985 levels. This "status quo scenario" results in a total of The study showed that Inco is the least-cost source for SO2 control. If Inco failed to reduce any of its SO2 emissions it would be difficult and exceedingly expensive to meet the provincial SO2 emission objective even with all industrial sectors at maximum technologically feasible control (and without any plant closures) . 40 If Ontario Hydro, the major stationary source of NO^ failed to reduce emissions below its 1985 levels, more stringent controls by mobile sources could compensate. A 10?o reduction below the 1994 SO2 status quo scenario would cost about $159 million in present value terms while a 30?o reduction would cost about $887 million or an additional $728 million. With a 50% reduction the price tag jumps to $5,338 billion. If Inco does not reduce its emissions below 1985 inventory levels, an expenditure of about $4.9 billion in present value terms would be required to reduce all other industrial sources to the maximum that is technologically feasible. Under this scenario, SO2 emissions would still total 1,019,000 tonnes per annum, higher than the 901 ,000 tonne level assumed in the status quo scenario. The second study listed, estimated the costs of achieving NO^ and Volatile Organic Compound (VOC) reductions at stationary sources in the Sarnia and the Hamilton-Toronto- Oshawa metropolitan regions. These pollutants are precursors to ozone formation. Stationary sources in the study region account for 42?o of the total provincial inventoried NOx emissions and 65?o of the total provincial stationary source VOC emissions. Stationary sources, however, are responsible for only a portion of total NO^ emissions. Transportation NOx, which was not covered by this study, accounted for 6ix% of total provincial NO^ in 1985. Estimates of the capital and operating cost and their distribution among industries and control technologies were developed for three control scenarios: Lowest Achievable Emission Rate (LAER) at all sources without closing plants, irrespective of economic achievability . Specified minimum control level applied to all emission sources (i.e., equal percent reductions at each emitter, regardless of cost) . Least-cost control to achieve successively lower levels of total emissions, from existing levels to LAER. Costs were estimated at individual emission sources in each plant in the study region for which emission data were available. Cost estimates of NOx abatement in the study on "future abatement strategies" were average costs of control applied to the total emissions in each industrial sector. Table 4 shows that the LAER level of VOC control can reduce controllable point source emissions in the study area by as much as 84?o, from 23,198 tonnes to 3,669 tonnes per year, at a cost of $22.4 million per year or $1,145 per tonne removed. Table 4: VOC Abatement Scenarios Sarnia & Oshawa-Toronto-Hamilton Metro Areas final Annual Scenario Emissions Cost (tonnes) ($) 1985 Emissions 23,198 0 from Control- lable Sources Min. 80?o 4,139 19,454,000 Reduction at Each Source 80% Reduction 4,711 15,555,000 at Least Cost LAER (84.2?o Red.) 3,669 22,364,000 NB: Capital Costs annualized at ^0% Source: VHB Research & Consulting Inc. , March 1989 - 41 - Table 4 also shows that reducing all controllable sources of VOC's in the region by at least 80?o would cost $19.5 million per year. However, a more selective application of emission targets at different sources could achieve a total 80% reduction of VOC emissions at a minimum total cost of $15.6 million per year. Table 5 shows that the LAER level of abatement for NO^ from stationary sources in the study area would reduce controllable emissions by 55?o, from 47,922 tonnes to 21,500 tonnes per year, at a cost of $320.0 million per year or $12,100 per tonne. Furthermore, a minimum reduction of 40?o could be achieved at all controllable NO^ sources in the study region at a cost of $61 .9 million per year or $3,191 per tonne of NOx removed. In contrast, abatement at the different stationary sources of NO^ considered in the area could be ranged so as to achieve a 40?o reduction in total emissions at a cost of only $50.0 million per year . The report also identifies the cost of specific VOC and NOx abatement technologies identified as "proven" for this study under the different scenarios. The study clearly shows that efficient abatement programs can be designed but that all sources would not have to reduce their emissions by the same degree under these programs. A scenario that appears to be more "equitable", in that each emitter will have to reduce by the same degree will be more costly to achieve. Control of VOC emitters from stationary sources is much more cost-effective than control of NO^ emissions (i.e., a lower cost per tonne removed). This means that VOC Table 5: NO^ Abatement Scenarios Sarnia & Oshawa-Toronto-Hamilton Metro Areas Final Annual Scenario Emissions Cost (tonnes) ($) 1985 Emissions 47,922 from Control- lable Sources 0 Min. 40?o 28,539 61,864,000 Reduction at Each Source 40?o Reduction 28,753 49,996,500 at Least Cost LAER (55. 1?^ Red.)21,500 319,974,500 NB: Capital Costs annualized at 10?o Source: VHB Research & Consulting Inc. , March 1989 emissions should be reduced before NOx °^ ^ cost basis unless there is evidence that relative degree of environment risk or harm attributable to NOx ^^ greater than for VOC. The Atmospheric Processes Studies section addresses this issue. The third study was intended to evaluate the cost effectiveness of vehicle emission control in Ontario and to assemble data on the populations of motor vehicles and other mobile sources of air pollutants. The study found that about 5 million cars and light duty trucks and 73,000 heavy duty vehicles are currently operating in Ontario. Emissions of NOx, ^^ ^^'^ hydrocarbons (VOC's) were estimated for these vehicles and for other mobile sources including aircraft, railways, ships, household engines, pleasure boats, and farm equipment. - l\l - Passenger cars and light duty trucks constitute the largest vehicle population and are the primary sources of pollutants. The study identified "Cases" or control scenarios for passenger cars: Case A assumes that new emission standards promulgated in 1987 by the federal government would continue. Case B assumes that three-way catalytic converters, capable of meeting a NOx emission standard of 0.4 gm/mile, plus pre-heaters and warm-up catalytic converts are required on all new cars, and thus a greater degree of emission control could be achieved from vehicles. Preliminary estimates from the report indicate that the marginal cost of NOx removal by adding three-way catalytic converters to new vehicles would amount to $1,777 per tonne of NOx removed (Case A to B). The marginal cost attributed to moving from Case A to Case B for CD control ranged from $709 to $940 per tonne of CO removed while hydrocarbon removal would cost between $614 and $11,606 per tonne removed, depending on the apportionment of joint costs to each pollutant. These studies indicate that NOx control at mobile sources appears to be much more cost effective than at stationary sources. - 43 LABORATORY SUPPORT SERVICES AND METHODOLOGY STUDIES Contact: P. Tomassini The Laboratory Services Branch provided analytical support to the scientific work groups within APIOS. A summary of the total test load for the program is shown in Figure 27. The largest increases in work were associated with analysis of trace organics in precipitation (17,500 tests) and vegetation analyses under the Maple dieback study (17,200 tests). The final total tests load for the program in 1988/89 was 357,800, an increase of 13.8?i over the 1987/88 fiscal year. Highlights for 1988/89 A new Varian AA400P atomic absorption spectrometer was purchased. If results are acceptable, the new instrument will be used to analyse both precipitation and surface water samples from the APIOS programs. Currently there are two older instruments providing this service. The data transfer routine via modem from Dorset to Toronto was successfully completed during the year. All LIS information from Dorset to Toronto is now updated twice weekly without the need for shipment of tapes. Full implementation of a new coding method (bar coding) for samples and submission information in Dorset is expected in the next year. Both the Toronto and Dorset laboratories continued to analyze samples submitted under an inter-comparison study spearheaded by the Federal laboratory in Burlington. A total of 54 laboratories from across North America are involved. Samples are submitted approximately 3 to 4 times a year. Twenty different sets of samples have been analyzed to date. During 1988/89 our laboratories participated in four of these inter-comparisons. Performance for both Toronto and Dorset laboratories was satisfactory. The average per cent Bias for the sample analysis on our data was 21.9. In many instances the magnitude of the bias for the Toronto laboratory was minor and insignificant for the demands of the data user i.e. less than 1?o of full scale for the test. Dorset was one of only five laboratories of the total of 54 to achieve a score of 0 in LRTAP inter-comparison #19. In these studies a score of less than 10?o is considered well done, 10-25?o is satisfactory, 25-60?o is moderate and greater than 6Q?o is poor. Method development is ongoing. The dependence of extractable iron and aluminum on soil particle size was investigated. Installation of a total carbon furnace attachment for the carbonate carbon analyzer was successfully completed. A comparison study between an automated method for colour measurement and the manual Klett- Summerson method was carried out. Comparisons between GFAAS and ASV methods for cadmium analysis, and comparisons between undigested and UV digested samples for cadmium continued . 44 - CO ■o C CO CO =J o o o CO ^^^^^ ^^^^^ ^^^^^ ^^^^^^ t^^^^^ ^^^ CD CO CO 00 CO o CO o o lO o o o o CO o o CM o o CO CO CO o Q_ < ,o I c o JO — CC r^ -*-• CVI CD CO o CJ Q u. - 45 ABATEMENT Contact: G. Endicott Since 1980, Ontario has been convinced that sufficient evidence existed to implement immediate SO2 controls while research continued to evaluate the benefits of these controls. As a result, Ontario was the first jurisdiction in North America to mandate emission controls based solely on the effects of long-range transport of air pollutants, as distinct from local ambient air quality standards. Ontario Hydro and Inco were the targets of these controls. In the absence of an acid rain agreement with the United States, the federal government and the seven Canadian provinces east of Saskatchewan decided in March 1984, to take unilateral action and reduce their sulphur dioxide emissions to a ceiling of 2.3 million tonnes by 1994, a 50?o reduction from the 1980 base case value. On February 5, 1985, they agreed to the series of steps to achieve the first 1 .9 million tonnes of this reduction and committed to determining the allocation of any further reductions in sufficient time to achieve the 1994 objective. Subsequently, Ontario went beyond the commitment it made at the federal/provincial meetings with its announcement of the Countdown Acid Rain program in December, 1985. Ontario will reduce sulphur dioxide emissions from the 1980 base case level of 2,194 kilotonnes to 885 kilotonnes by 1994. Four non-appealable regulations were issued to the four corporate sources which together emit 80?o of Ontario's SO2: Inco, Falconbridge, Algoma Steel (Wawa) and Ontario Hydro. The regulated annual emission limits were developed in consultation with each of the major pollution sources to ensure that economic activity need not be excessively inhibited. A phase-in approach is taken. Regulated limits are summarized below (Table 6) . Table 6: Legal Limits for SO2 for the four companies Source Legal Limits Sulphur Dioxide 1986 1994 (thousands of metric tonnes per year) Inco, Sudbury 685 265 Falconbridge, Sudbury 154 100 Algoma, Wawa 180 125 Ontario Hydro, province-wide 370 175 A fifth regulation limits 5O2 emissions from new or modified boilers by placing a 1 per cent sulphur content constraint on the fuel or by requiring that an equivalent amount of 5O2 be removed from the flue gas. In addition to the SO2 limit, the sum of SO2 and NO emissions is also regulated for Ontario Hydro. 46 Furthermore, there are interim limits by 1990 (Table 7). Table 7: Ontario Hydro's Acid Gas Limits 50? SO7 + NO (Kilotonnes/Yr) 1986-1989 370 430 1990-1993 240 280 1994 + 175 215 Control technologies were not specified so that the individual companies may choose their method of abatement. The regulations only require that the legal limits are met by the specified dates. The regulations provide for a three year research and development period. Semi-annual interim progress reports are required from the four major companies, and they are reviewed by experts from various Ontario ministries. A final report was received on December 31, 1988 from each of the metallurgical companies and in January, 1989 from Ontario Hydro. These reports clearly stated that the companies would be able to meet the regulated limits, and the reports described precisely how the emission limits would be met. The government's summary and analysis of all these reports along with copies of the company reports are available upon request. Countdown Acid Rain will do more than just help Ontario's environment; it will also reduce acid rain in Quebec and the northeastern United States. However, the major emission reductions in Ontario and elsewhere in eastern Canada will not be sufficient to protect the environment. Major emission reductions are also required in the United States. All Canadian attempts to negotiate a bilateral treaty on acid rain with the United States failed during the Reagan Administration. While President Reagan reaffirmed his commitment to clean coal technology development and agreed to consider the possibility of an accord, there had been no significant progress made. President Bush has committed to a Bill to control acid rain. The proposed Bush Bill was announced on June 12, 1989 and details given on July 21, 1989. In essence, the Bill calls for a two-phase reduction of SO2; 5 million tons (including a 1 million ton reduction which has already occurred) by 1995 and another 5 million tons by 2000 with respect to the 1980 base case. A reduction of 2 million tons of NO^ is also proposed in the Administration Bill. There are provisions for utility and pollutant trading and an extension to the year 2003 if clean coal technology is employed in the repowering. The proposed Bill is clearly a step forward. Timing for signing legislation is uncertain as debates and changes made to the Bill are expected at Congress. In addition to the domestic Bill, a U.S. -Canada accord on acid rain will also be developed. - 47 COMMUNICATIONS INITIATIVES Contact: G. Merchant The Communications Work Group (with representatives from the Ministries of Intergovernmental Affairs, Tourism and Recreation, and Natural Resources), discussed and implemented strategies to increase awareness of acid rain among Ontario and American citizens. ONTARIO Ontario citizens are aware of acid rain as evidenced by the number of information requests made directly to the APIOS Coordination Office. 587 individualized packages of information were mailed in this fiscal year and about 500 people visited the Office. As well, there were numerous presentations to schools and interest groups. These contacts are over and above the enormous quantity of requests for acid rain information and the fish poster handled directly by the Communications Branch. In total, approximately 260,000 brochures and posters were sent to Canadian and American citizens. UNITED STATES The communications strategy directed toward targeted U.S. audiences stresses several themes: Human Health - Evidence has been accumulating that acid gas emissions are detrimental to human health. Out of the Trenches - Instead of focussing on the stalemate between those in the northeastern and midwestern states, people in other regions of the U.S. are being made aware of their stake in the issue. Effective American Legislation Is Required - There is a need for an interim and longer-term cap on acid gas emissions to prevent back-sliding and reach a scientifically supportable critical loading. The sooner the better. Biological systems tolerate considerable stress before suddenly crashing. It Can Be Done - Cost-effective acid rain abatement technology options do exist. There are specific economic benefits of abatement in the creation of a strong environmental protection industry. Ontario's Countdown Acid Rain program serves as a model of a successful abatement program. This approach is intended to increase Americans' awareness of acid rain and of the solutions that do exist. To this end, several initiatives were undertaken and included the following: Ontario was the lead agency in organizing three acid rain information trips to Canada for a 48 total of 17 congressional legislative assistants. These included visits to Toronto, the Dorset research centre, Sudbury, Ottawa and Quebec. Meetings were held with federal and provincial political leaders, the Canadian Coalition on Acid Rain, and executives from Inco, Ontario Hydro and Falconbridge. A similar information trip was conducted for seven U.S. journalists in July. A pamphlet entitled "It Falls On All Of Us" was developed to present key statements on acid rain. It proved to be popular and more than 140,000 copies were distributed to the American public. The Ministry of the Environment and Trout Unlimited jointly organized a mail-out of Ontario and federal government acid rain information pamphlets to Trout Unlimited members (43,000). The mail out was arranged for July 1988. Trout Unlimited has reported that it will continue to prompt its members to write their government representatives as new acid rain control bills enter Congress. This joint program evolved from a contact made at Trout Unlimited's 28th National Convention (August 1987), attended by APIOS representatives. Similar to previous years, an acid rain display was exhibited and staffed by Ministry personnel at several international conferences and shows: The Air Pollution Control Association's annual conference in Dallas, Texas; The Arizona Commission On The Environment's annual conference in Prescott; Canada Day at the State University of New York in Plattsburgh; and the Cincinatti Sport, Boat and Camp Show. The display was well-received at all four shows and many valuable contacts were made. In December 1988, staff from APIOS, Communications, Legal Services and the Minister's Office attended a Bi-National meeting on opportunities for controlling acid rain. Minister Bradley delivered the keynote speech which was the winner of an Ontario Information Officers FORUM award. In February 1989, the Minister delivered a speech on the health effects of acid rain to the National Issues Conference at Marshall University, Charleston, West Virginia. A similar speech was given to over 17 different media representatives at the National Press Club in Washington, D.C. The speech was subsequently aired three times over The C-Span network — the internal broadcast network which services all members of Congress. After the speech, the Minister and representatives from APIOS, Communications and the Canadian Embassy attended separate meetings with six senators and the new EPA director. The Ministry of the Environment participated in the Harrisburg Pennsylvania Sportsman Show in collaboration with the Alliance for Acid Rain Monitoring (ALLARM), a Pennsylvania-based volunteer organization. The MOE rented exhibit space and provided ALLARM with some publications. ALLARM provided their exhibit and staff. For the second and final year, a tear-off card requesting information on acid rain was provided with the application form for all non- resident angling licenses. In 1987, 10,000 requests were received out of 300,000 licenses issued. In 1988, 5,679 requests were received out of approximately 300,000 licenses issued. This drop in the number of requests is probably attributable to a lack of requests for updated acid rain information by anglers who received our information the year before. LEGAL INITIATIVES - 49 - Contact; 1. Carr Under the Memorandum of Intent signed in 1980, Canada and the United States agreed to enforce existing laws and regulations responsive to the problems of transboundary air pollution. Since 1981, however, the Unites States Environmental Protection Agency has proposed the approval of revisions in State Implementation Plans (S.I.P.'s) under section 110 of the U.S. Clean Air Act which would lead to increases in allowable sulphur dioxide emissions from coal-fired power plants. Because increased emissions could affect the province's environmental quality, Ontario encouraged the U.S. EPA Administrator and state governments to disapprove any S.I. P. revisions which would result in any increase in permissible emissions of SO2 in the U.S. Seeking an a rain control has appeared and particip proceedings efforts have conjunction states, envi groups, and directed at Unites State sections 115 venue to effective acid s in the U.S., Ontario at numerous hearings ated in judical since 1981 . These been made in with several American ronmental interest citizens, and are two key parts of the s Clean Air Act: and 126. Section 126 provides for the intervention of the EPA's Administrator in instances when interstate air pollution can be shown to be preventing the attainment of national abatement air quality standards, or interfering with those prevention of significant deterioration or visibility measures which the Act requires to be included as a part of a state implementation plan. This path to acid rain controls was blocked in March 1989, when the U.S. Supreme Court said it would not hear an appeal by a group of northeastern states. This decision means that an earlier ruling by the U.S. Circuit Court of Appeals will stand. That court ruled the EPA was not required to force reductions of pollution originating in other states since the northeastern states did not adequately support their claims of injury. Ontario has been more actively involved in proceedings dealing with the internationally-oriented section 115. This section provides, in pertinent part: (a) Whenever the (EPA) Administrator, upon receipt of reports, surveys or studies from any duly constituted international Agency has reason to believe that any air pollutant or pollutants emitted in the United States cause or contribute to air pollution which may reasonably be anticipated to endanger public health or welfare in a foreign country ... the Administrator shall give formal notification thereof to the Governor of the state in which such emissions originate. - 50 Under section 115 the Administrator agency to take similar action under also has to make findings that the section 115. This was joined by the foreign country offers reciprocal National Audubon Society. Once rights to the United States and that formal findings are made the EPA is the environment of the foreign then required to compel states from country is endangered. which offending emissions come to reduce their emissions. In April 1988, Ontario and a group of states filed independent petitions to the U.S. EPA Administrator requesting that he reaffirm findings of endangerment and reciprocity under section 115 which had been made informally in 1981 by the Administrator of the EPA and accepted in previous court actions, by publishing the findings in the Federal Register and then promulgating the findings as final rules. In October, 1988 the Acting Assistant Administrator of EPA's Air and Radiation Office issued a response stating that it would be premature for EPA to take any rule making action until NAPAP findings are available for assessment in 1990. In November 1988, a follow-up legal petition was submitted to the U.S. Circuit Court of Appeals for the District of Columbia by Ontario to require the U.S. EPA to formally make the findings of reciprocity and endangerment. The suit was joined by two U.S. environmental groups, the Sierra Club Legal Defence Fund and the Izaak Walton League of America. Later, the Federal Government, Quebec, New Brunswick, and other Canadian environmental groups requested to become Amici Curiae (friends of the court) in support of Ontario. Also in November, 1988, nine states (6 New England states, plus New York, New Jersey and Minnesota) also filed a parallel lawsuit against the U.S. EPA to force the 51 - a. 0) QJ (D CJ il > Q. (D cn Q. E o :3 ^X3 CC O (D jC O ^ jj J= tj t-i ^-- -u - (-. O Ld CO czr C (D cn CSS 4-) O (U J-J -H 0) o c -H -o c s: z Q- (D tj c (D E o tj cn rH (-. (D (D .f-t o CD •rH 4J 4-) > E S > CD CD c 4-1 E c 4-1 4-) LJ c o C -H C (D C 13 4-1 CD CD (D (-1 >N O cn E E E CD £-1 (D CD C C 4-) -U J3 (D O O t- S cn CD n U (-1 CD (D ■H D 4-1 ■H •H D.Z C C3- (-< > > CO o O Q Q.«3: .-« D CD cn CO cc (D O en u Q. u C E Q. S CO JJ -H >^ --H CD O X! ^ >-* C (D 13 CD -I-) C O O E "O O C (D (-1 52 "O (D CD O CD "D -U O CO C (D Q. cn D. >^ c •H JH >.4-l o ^ -H o. 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CD E -u 57 - APPENDIX II API05 RELATED TECHNICAL REPORTS AND SUBMISSIONS 1989 A Survey to Document the Decline Status of Hardwood Forests in Ontario - 1987 by Ecological Services for Planning Limited in Guelph. API0S-12-B9. Acid precipitation research in Canada. 1989. 3.C. Keith and P.J. Dillon. Ont. Min. Envir. Tech. Rep. 52 pp. An Investigation of the Use of Lichens and Mosses as Biomonitors of Acidic Precipitation in Ontario. Case Biomanagement . APIOS-014-89. Annual retention of ammonium and nitrate and short-term ionic composition of streamwater during snowmelt in lakes and forested catchments in Ontario. 1989. P.J. Dillon and L.A. Molot. Ont. Min. Envir. Tech. Rep. 128 pp. Assessment of Sugar Maple and Yellow Birch Foliage and Soil Chemistry at the Ontario Hardwood Decline Survey Plots. Ecological Services for Planning Limited. APIOS-01 3-89 . Changes in the Decline Status of Hardwood Forests in Ontario. 1986-1987. APIOS-012-89. Modelling of Ozone Production on the Sarnia Region. N. Reid and S. Wong. 1989. MOE Report ARB-205-88. Ontario Emissions Inventory Report System. 1989. User Guide. 1988 1985 Ontario Emission Inventory for Cadmium, Manganese, Arsenic and Iron, Vol. 1-3, EAG, December 1988. A Survey to Document the Decline Status of the Sugar Maple Forest of Ontario: 1986-1987. APIOS-010-88. Alkaline Dust and Ammonia Emissions Inventory for Ontario, Vol. 1-3, EAG, March 1988. APIOS 1986 Daily Ambient Air Concentration Listings. D. Green. ARB-036-88. APIOS-004-88. APIOS 1986 Daily Precipitation Chemistry Listings. D. Green. ARB-035-88. APIOS-003-88. APIOS Annual Statistics of Concentration and Deposition - Cumulative Precipitation Monitoring Network, 1986. D. Green. ARB-039-88. APIOS-007-88. APIOS Annual Statistics of Concentration and Deposition - Daily Precipitation and Air Monitoring Network, 1986. D. Green. ARB-038-88. APIOS-006-88. - 58 - 1988 (continued) APIOS Annual Statistics of Concentration Cumulative Ambient Air Monitoring Network, 1986. D. Green. ARB-037-88. APIOS-005-88. APIOS Cumulative (28-day) Ambient Air Concentration Listings, 1986. D. Green. ARB-033-88. APIOS-001-88. APIOS Cumulative (28-day) Precipitation Chemistry Listings, 1986. D. Green. ARB-034-88. APIOS-002-88. Chemical and biological data summary for Plastic outflow acidification experiments (spring and autumn, 1982). 1988. J. Findeis. Ont. Min. Envir. Data Report DR 88/2. Chemical and biological summary for Lake 222 outflow acidification experiments (Experimental Lakes Area) (May 1983). 1988. J. Findeis, R.J. Hall and M. Coleman Taylor. Ont. Min. Envir. Data Report DR 88/3. Consolidation of Available Emission Factors for Selected Toxic air Pollutants, GRF, November, 1988. Effects of Acidic Precipitation and Related Pollutants in the Terrestrial Environment: A Program Description. Mcllveen, W.D. and S.N. Linzon. 1988. ARB-218-87-Phyto. API0S-008-88. 26 pp. Etiology of Sugar Maple Decline at Selected Sites in Ontario (1984-1988). API0S-011-88. Lake Neutralization Summary Report. API0S-009-88. Muskoka lakes project: A progress report of the 1986 data. 1988. R.A. Reid. Ont. Min. Envir. Data Report DR 88/1. 1987 An Assessment of Source Contributions to the Ozone Concentrations in Southern Ontario 1979 - 1985. Yap, D. , Ning, D.T. and Dong, W. Ontario Ministry of the Environment Report No. ARB-101-87-AQM. An Assessment of the Current Impact and Potential Risks of Acid Deposition on Smallmouth Bass Populations in Ontario. J.E. Matuszek. 1987. Ont. Fish. Acid. Tec. Rep. Ser. 87-09. 20 pp. Annual Statistics of Concentration and Deposition - Cumulative Precipitation Monitoring Network 1985. APIOS #002/87. Annual Statistics of Concentration and Deposition - Cumulative Precipitation Sites in Industrial/Urban Areas in Ontario. January 4, 1983 - January 15, 1985. APIOS #001/87. APIOS 1985 Daily Ambient Air Concentration Listings. D. Green. ARB-89-87-AQM. - 59 - 1987 (continued) APIDS 1985 Daily Precipitation Chemistry Listings. D. Green. ARB-005-87-AQM. APIOS Annual Statistics of Concentration and Deposition - Daily Precipitation and Air Monitoring Network, 1985. D. Green. ARB-087-87-AQM. APIOS Annual Statistics of Concentration - Cumulative Ambient Air Monitoring Network, 1985. D. Green. ARB-086-87-AQM. API OS-01 3-87. APIOS Cumulative Ambient Air Concentration Listings - January 4, 1985 - January 7, 1986. D. Green. ARB-88-87-AQM. APIOS Statistics of Concentration and Deposition - Cumulative Precipitation Sites in Industrial Urban Areas in Ontario. January 4, 1983 - January 15, 1985. D. Green. ARB-004-87-AQM, ISBN #0-7729-2134-2, API0S-001-87-AQM. Chaoborus abundance in Muskoka-Haliburton Lakes: 1986 Methods and Data. 1987. T.W. Pawson and L.J. McEachern. Ont. Min. Envir. Data Report DR 87/3. Efficiency of Aquatic Habitat Inventory Surveys in the Assessment of Fish Species Present. Bowlby, J.N. and D. Green. 1987. Ont. Fish. Acid. Rep. Ser. 87-08. 39 pp. Lakeshore Capacity Study - Trophic Status. 1987. P.J. Dillon, K.H. Nicolls, W.A. Scheider, N.D. Yan and D.S. Jeffries. Ont. Min. Municip. Affairs Rep. 89 pp. Literature Review in Table Form of Toxic Responses of Freshwater Fish to Acid and Metals. E.L. Hofman. 1987. Ont. Fish. Acid. Tec. Rep. Ser. 87-07. Maple Decline in Ontario: Situation/Research Status Report. D.L. McLaughlin. 1987. Presented at Maplefest '87 at Grand Falls, New Brunswick, June 12 - 13, 1987. 11pp. Morphometric, chemical, physical and geological data for Axe, Brandy, Cinder, Fawn, Healey, Leech, Leonard, McKay, Moot, Poker, Red Pine Lakes in the Muskoka-Haliburton area (1978-1985). 1987. R.A. Reid and G. Girard. Ont. Min. Envir. Data Report DR 87/2. Morphometric, chemical, physical and geological data for Axe, Brandy, Cinder, Fawn, Healey, Leech, Leonard, McKay, Moot, Poker, Red Pine Lakes in the Muskoka-Haliburton area (1978-1985). 1987. R.A. Reid and G. Girard. Ont. Min. Envir. Data Report DR 87/2 (Appendix). Morphometry and catchment areas for the calibrated watersheds. 1987. R.A. Reid, R. Girard and A.C. Nicolls. Ont. Min. Envir. Data Report DR 87/4. Observation of Lake Trout (Salvelinus namaycush) Spawning Behaviour in Low pH Lakes Near Sudbury, Ontario. Liimatainen, V.A., Snucins, E.J. and J.M. Gunn. 1987. Ont. Fish. Acid. Rep. Ser. 87-10. 71pp. - 60 - 1987 (continued) Preliminary Assessment of the Current Impact and Potential Risk of Acidic Deposition on Walleye Populations in Ontario. Wales, D.L. and V.A. Liimatainen. 1987. Ont. Fish. Acid. Rep. Ser. 87-11. 51pp. Physical and chemical data for Bonnechere, Big Porcupine, Crown, Kimball, Louisa, Nunikani, Sherborne, Smoke, and Timberwolf Lakes in the Muskoka- Haliburton area (1983-1985). 1987. R.A. Reid and R. Girard. Ont. Min. Envir. Data Report DR 87/1. Review and Update of Bio-Economic Models of Acid Deposition. The DPA Group Inc. 1987. Ontario Ministry of the Environment, Policy and Planning Branch. Technical and Operating Manual. APIOS Deposition Program. APIOS #003/87. 1986 Abundance of Chaoborus Larvae in Chub Lake: Sampling Methods and 1982 data. Lasenby, D.C., Morris, K. and N.D. Yan. Ont. Min. Env . Data Report DR 86/3. Abundance of Chaoborus larvae in Chub Lake: sampling methods and 1982 data. 1986. D.C. Lasenby, K. Morris and N.D. Yan. Ont. Min. Envir. Data Report DR 86/3. A Historical Perspective of Sugar Maple Decline Within Ontario and Outside of Ontario, December 1986. Mcllveen, W.D. , Rutherford, S.T. and S.N. Linzon. APIOS #010/86 ARB-141-86-Phyto. A Unified Wet Deposition Data Base for Eastern North America: Addendum with Results for Sulfates and Nitrates (1980 - 1983). Prepared by the Unified Deposition Data Base Committee (M. Lusis, Coordinator), 1986. An Analysis of the Effects of the Sudbury Emission Sources on Wet and Dry Deposition in Ontario. Tang, A.J.S., Chan, W.H. and M.A. Lusis. ARB-124-84-ARSP, 1986. An Evaluation of Sampler Types and Sampling Periods for Measurements of Wet and Dry Deposition. Chan, W.H., Tang, A.J.S., Bardswick, W.S., Orr, D. and M.A. Lusis. Report ART-098-85-AQM, 1986. APIOS 19-85. Assessment of Aquatic and Terrestrial Acidic Precipitation Sensitivities for Ontario. D.W. Cowell. Joint Federal/ Provincial. APIOS #009/86, ARB-220-86-Phyto. Estimation of the Presence and Impact of Filamentous and Odour-Producing Algae: A Survey of Cottagers on 214 Ontario Recreational Lakes. SPR Associates Inc. 1986. Ontario Ministry of the Environment. - 61 - 1986 (continued) Geology of Big Porcupine, Clear, Crown, Nunikani and Sherborne cathcments (Haliburton County). 1986. R.A. Reid and W.R. Snyder. Ont. Min. Envir. Data Report DR 86/1 . Inventoried Air Pollution Emissions of Sulphur Dioxides, Nitrogen Oxides and Volatile Organic Compounds for the Province of Ontario (1980 - 1983). Wong, S.K.S., Yap, D. and Huynh, Q.I. Ontario Ministry of the Environment Report No. ARB-187-86-AQM. Meteorological data base for the Muskoka-Haliburton Area. 1986. B.A. Locke and E. de Grosbois. Ont. Min. Envir. Data Report DR 86/5. Precipitation and Air Concentration and Wet and Dry Deposition Field of Pollutants in Ontario, 1983. Acidic Precipitation in Ontario Study. ARB-G08-86-AQM. API0S-001-86 . Procedures Manual - Terrestrial Effects. Acidic Precipitation in Ontario Study (APIOS). ARB-93-86-Phyto. February 1986. Studies of Lakes and Watersheds in Muskoka-Haliburton, Ontario: Methodology (1976-1985). Locke, B.A. and L.D. Scott. Ont. Min. Env . Data Report DR 86/4. Studies of lakes and watersheds in Muskoka-Haliburton, Ontario: methodology (1976-1985). 1986. B.A. Locke, L.D. Scott. Ont. Min. Envir. Data Report DR 86/4. Summary: Some Results from the APIOS Atmospheric Deposition Monitoring Program (1981 - 1984). Tang, A.3.S., Ahmed, A. and M.A. Lusis. ARB-110-86, APIOS-011-86. Susceptibility of Lake Trout (Salvelinus namaycush) Spawning Sites in Ontario to Acidic Meltwater. M.J. McMurty. 1986. Ont. Fish. Acid. Rep. Ser. No. 86-01 . 20 pp. The Chemical Sensitivity of Lakes to Acidic Deposition and the Risk to Fish Populations: Algonquin Region. D. Conrad. 1986. Ont. Fish. Rep. Ser. 84-02. 59 pp. The Chemical Sensitivity of Lakes to Acidic Deposition and the Risk to Fish Populations: North Central Region. D. Conrad. 1986. Ont. Fish. Rep. Ser. 84-03. 38 pp. The Chemical Sensitivity of Lakes to Acidic Deposition and the Risk to Fish Populations: Northeastern Region. D. Conrad. 1986. Ont. Fish. Rep. Ser. 84-04. 54 pp. The Chemical Sensitivity of Lakes to Acidic Deposition and the Risk to Fish Populations: Northern Region. D. Conrad. 1986. Ont. Fish. Rep. Ser. 84-05. 54 pp. - 62 1986 (continued) The Chemical Sensitivity of Lakes to Acidic Deposition and the Risk to Fish Populations: Northwestern Region. D. Conrad. 1986. Ont. Fish. Rep. Ser. 84-06. 54 pp. User Manual for the Lab Information System (LIS), Dorset Research Centre. Nicolls, A., Locke, B.A. and S.A. McCormick. Ont. Min. Env . Data Report DR 86/2. 1985 1983 Daily Precipitation Chemistry Listings. APIOS Report No. 004/85. Acidic Precipitation in Ontario Study, 1984 Daily Ambient Air Concentration Listings. Report ARB-195B-85. Acidic Precipitation in Ontario Study, 1984 Daily Precipitation Chemistry Listing, Report ARB-247-85. Acidic Precipitation in Ontario Study, 1983 Daily Precipitation Chemistry Listing. Report ARB-043-85-AQM . APl-004-05. Acidic Precipitation in Ontario Study, An Overview: The Cumulative Wet/Dry Deposition Network (Second Revised Edition). Report ARB-1 41-85-AQM. APIOS-024-85. Acidic Precipitation in Ontario Study, An Overview: The Event Wet/Dry Deposition Network (First Revised Edition). Report ARB-1 42-B5-AQM. APIOS-025-85. Acidic Precipitation in Ontario Study, Cumulative (28 day) Precipitation Chemistry Listings, January 3, 1984 - January 2, 1985. Report ARB-239-85. Acidic Precipitation in Ontario Study, Cumulative Ambient Air Concentration Listings, December 6, 1983 - January 3, 1985. ARB-195A-85. Air Concentration and Dry Deposition Fields of Pollutants in Ontario, 1982. APIOS Report No. 001/85. An Assessment of the Performance of the Daily Precipitation and Air Sampling Networks, July 1980 - December 1981. Acidic Precipitation in Ontario Study. Report ARB-100-85-AQM. Annual Statistics of Concentration - Cumulative Ambient Air Monitoring Network, 1984. Acidic Precipitation in Ontario Study. Report ARB-237-85-AQM. Annual Statistics of Concentration - Cumulative Ambient Air Monitoring Network, 1983. Acidic Precipitation in Ontario Study. Report ARB-089-85-AQM. - 63 1983 (continued) Annual Statistics of Concentration and Deposition - Cumulative Precipitation Monitoring Network, 1984. Acidic Precipitation in Ontario Study. Report ARB-235-85-AQM. Annual Statistics of Concentration and Deposition - Cumulative Precipitation Monitoring Network, 1983. Acidic Precipitation in Ontario Study. Report ARB-087-B5-AQM. Annual Statistics of Concentration and Deposition - Cumulative Precipitation Sites in Industrial/Urban Areas in Ontario, 1981 and 1982. APIOS Report No. 005/85. Annual Statistics of Concentration and Deposition - Daily Precipitation and Air Monitoring Network, 1984. Acidic Precipitation in Ontario Study. Report ARB-236-85-AQM. Annual Statistics of Concentration and Deposition - Daily Precipitation and Air Monitoring Networks. Acidic Precipitation in Ontario Study, 1983. Report ARB-109-85-AQM. Bryophyte Floras of Acid-sensitive Lakes in South-central Ontario: Description and Mechanisms of Sphagnum Invasion. Manville, G.C. and N.D. Yan. 1985. Ont. Min. Envir. Tech. Rep. 22pp. The Case for Effects of Acid Deposition on Ontario Fisheries. Beggs, G.L., Maclean, 3. A., Gunn, 3.M., Jones, M.L., and K, Minns. 1985. U.S. Fish Wildlife Serv. Biol. Rept. 80(40.21), 49-61. Cumulative (28 Day) Precipitation Chemistry Listings, January 4, 1983 - January 4, 1984. Acidic Precipitation in Ontario Study. Report ARB-063-85-AQM. Cumulative (28 Day) Precipitation Chemistry Listings of Sites in Industrial/Urban Areas in Ontario, September 1980 - January 1983. APIOS Report No. 003/85. Cumulative Ambient Air Concentration Listings. January 4, 1983 - January 3, 1984. Acidic Precipitation in Ontario Study. Report ARB-088-85-AQM. Daily Ambient Air Concentration Listings. Acidic Precipitation in Ontario Study. Report ARB-108-85-AQM. An Evaluation of Sampler Types and Sampling Periods for Measurements of Wet and Dry Deposition. Chan, W.H., Tang, A.J.S., Bardswick, W.S. , Orr, D. and M.A. Lusis. Report ARB-098-85-AQM. APIOS-019/85 . The Economics of Acid Precipitation: A Review of Socio-Economic Methods to Assess Acid Deposition Effects. Ontario Ministry of the Environment, Corporate Policy and Planning Branch (April, 1984: Reprinted w;ith Corrections, July 1985). Ontario Ministry of the Environment. 64 1983 (continued) The Morphometry and Geology of Plastic and Heney Lakes and Their Catchments. Girard, R., Reid, R.A. and W.R. Snyder. Gnt. Min. Env . Data Report DR 85/1. The morphometry and geology of Plastic and Heney Lakes and their catchments. 1985. R. Girard, R.A. Reid and W.R. Snyder. Gnt. Min. Envir. Data Report DR 85/1. Ontario Soil Baseline Survey Analytical Data 1980/81. APIOS Report No. 002/85. Three Volumes. Quality Assurance Management Programme for the Limnology Unit, Dorset Research Centre. Locke, B.S. Ont. Min. Env. Data Report DR 85/4. Quality Assurance Manual. Deposition Monitoring Networks. Acidic Precipitation in Ontario Study. APIOS Report No. 006/85. February 1985. Quality assurance management programme for the Limnology Unit, Dorset Research Centre. 1985. B.A. Locke. Ont. Min. Envir. Data Report DR 85/4. The Sarnia Oxidants Study (June 27 - Duly 18, 1984): Analysis of the Air Quality and Meteorological Data. Lusis, M.A. , Sahota, H. and D. Yap. Report ARB-124-85-AQM. The Sarnia Oxidants Study (June 27 - July 18, 1984): Report on the Airborne Measurements. Sahota, H. , Kiely, P. and M. Lusis. Report ARB-019-85-ARSP. The Sensitivity of Ontario Lake Trout (Salvelinus namaycush) and Lake Trout Lakes to Acidification. Beggs, G.L., Gunn, J.M. and C.H. Olver. 1985. Ont. Fish. Tech. Rep. Ser. No. 17: 24pp. Sugar Maple Decline in Ontario. McLaughlin, D.L., Linzon, S.N. , Dimma, D.E. and W.D. Mcllveen. Report ARB-1 44-85-Phyto. APIOS 026/85. Temperature and Oxygen Data for the Muskoka-Haliburton Study Lakes (1983-1984). Reid, R.A. and R. Girard. Ont. Min. Env. Data Report DR 85/2. Temperature, Oxygen, pH and Dissolved Inorganic Carbon Data Summary for Eight Lakes in the Muskoka-Haliburton Study Area (1982-1984). Girard, R. and R.A. Reid. Ont. Min. Env. Data Report DR 85/3. Temperature and oxygen data for the Muskoka-Haliburton study lakes (1983-1984). 1985. R.A. Reid and R. Girard. Ont. Min. Envir. Data Report DR 85/2. Temperature, oxygen, pH and dissolved inorganic carbon data summary for eight lakes in the Muskoka-Haliburton study area (1982-1984). 1985. R. Girard and R.E. Reid. Ont. Min. Envir. Data Report DR 85/3. - 65 - 1985 (continued) A Unified Wet Deposition Data Base for Eastern North America: Data Screening, Calculation Procedures, and Results for Sulphates and Nitrates (1980). Prepared by the Unified Deposition Database Committee (M. Lusis, Coordinator), 1985. Water Quality Changes in Sudbury area lakes, 1974-76 to 1982-83. Keller, W. and J.R. Pitblado. Ont. Min. Env. Tech. Rep. APIOS 007/85. 29 p. 1984 1982 Daily Ambient Air Concentration Listings. APIOS Report No. 004/84. 1982 Daily Precipitation Chemistry Listings. APIOS Report No. 002/84. An Analysis of the Effects of the Sudbury Emissions Sources on Wet and Dry Deposition in Ontario. Tang, A.J.S. and W.H. Chan. APIOS Report No. 011/84. An Assessment of the Performance of the Cumulative Precipitation Monitoring Network - June, 1980 - December, 1981. Acidic Precipitation in Ontario Study. W.S. Bardswick. Report ARB-143-84-ARSP . Annual Program Report - Fiscal Year 1983/1984. APIOS Report No. 010/84. Annual Program Report - Fiscal Year 1982/1983. APIOS Report No. 001/84. Annual Statistics of Concentration, Cumulative Ambient Air Monitoring Network, 1982. APIOS Report No. 015/84. Annual Statistics of Concentration and Deposition - Cumulative Precipitation Monitoring Network, 1982. APIOS Report No. 008/84. Annual Statistics of Concentration and Deposition - Daily Precipitation and Air Monitoring Network, 1982. APIOS Report No. 009/84. Cumulative (28 Day) Precipitation Chemistry Listings - January 5, 1982 - January 4, 1983. APIOS Report No. 003/84. Cumulative Ambient Air Concentration Listings August 31, 1981 - January 4, 1983. APIOS Report No. 013/84. Data Report - Monitoring of Northeastern Ontario Lakes, 1981-83. Pitblado, J.R. and W. Keller. 1984. Ontario Ministry of the Environment Technical Report. 9 pages plus appendices. The Economics of Acid Precipitation: A Review of Socio-Economic Methods to Assess Acid Deposition Effects. APIOS Report No. 006/84. Emission Inventory of Ontario and Eastern North America during 1980-1983 with Emphasis on the Sudbury Shut-down Period. D. Yap. APIOS Report No. 016/84. 66 1984 (continued) Examination of Monthly Wet Sulphate Deposition by a Lagrangian Model and its Application to Study the Effects of Source Control on Receptors. Ellenton, G. and P.K. Misra. APIOS Report No. 018/84. Macrophyte Data from 46 Southern Ontario Soft Water Lakes of Varying pH. Hitchin, G.G., Wile, I., Miller, G.E. and N.D. Yan. Ont. Min. Env . Data Report DR 84/2. Macrophyte data from 46 southern Ontario soft water lakes of varying pH. 1984. G.G. Hitchin, I. Wile, G.E. Miller and N.D. Yan. Ont. Min. Envir. Data Report DR 84/2. Meteorological Studies to Quantify the Effects of Sudbury Emissions on Precipitation Quality and Air Quality During 1980-1983 with Emphasis on the Shut-down period. Kurtz, J. and D. Yap. APIOS Report No. 17/84. An Overview of the Cumulative Wet/Dry Deposition Network. APIOS Report No. 007/84. An Overview: The Cumulative Wet/Dry Deposition Network. Chan, W.H., Orr, D.B. and R.J. Vet. APIOS Report No. 005/84. Physical and chemical data summary for twelve selected lakes in the Muskoka-Haliburton area (1981-1983). 1984. R.A. Reid, B.A. Locke, R.E. Girard and A.C. Nicolls. Ont. Min. Envir. Data Report DR 84/1. Precipitation Concentration and Wet Deposition fields of Pollutants in Ontario, 1982. APIOS Report No. 012/84. Quality Assurance Plan - APIOS Deposition Monitoring Program. Summary: Source Apportionment Analysis of Air and Precipitation Data to Determine Contribution of the Sudbury Smelters to Atmospheric Deposition in Ontario. Lusis, M.A. APIOS Report No. 019/84. 1983 1981 Summary Statistics of Observed Concentration and Deposition: Daily Precipitation Monitoring Network. Kirk, R.W. and W.H. Chan. June 1983. Acid Sensitivity Survey of Lakes in Ontario. APIOS Report No. 001/83. Acidic Precipitation in Ontario Study - Technical and Operating Manual, APIOS Deposition Monitoring Program. Bardswick, W.S. April 1983. Annual Statistics of Concentration and Deposition - Cumulative Precipitation Monitoring Network, 1981. Kirk, R.W. September 1983. Annual Statistics of Concentration and Deposition - Cumulative Precipitation Monitoring Network, 1981. Kirk, R.W. August 1983. APIOS Report No. 008/83. - 67 - 1983 (continued) APIOS Daily Precipitation Chemistry Listings, July 15, 1980 - December 31, 1981. Revised Edition January 1983. APIOS Monthly/28 Day Cumulative Precipitation Chemistry Listings, June 1980 - December 1981. March 1983. Area Source Emission Inventory for Nitrogen Oxides in Ontario by Ontario Research Foundation for MOE. Final Report (Proposal No. p-4261/G). September 1983. Crustacean zooplankton communities of the Muskoka-Haliburton study lakes: methods and 1976-79 data. G.G. Hitchin and N.D. Yan. Ont. Min. Envir. Data Report DR 83/9. Daily Ambient Air Concentration Listings, July 25, 1980 - December 31, 1981. May 1983. Depth and Volume of Strata in the Muskoka-Haliburton Study Lakes (1976-1982). Girard, R., Locke, B.A. and R.A. Reid. Ont. Min. Env . Data Report DR 83/10. Effects of pH and ionic strength on Al toxicity to early developmental stages of rainbow trout (Salmo gairdneri Richardson). 1983. K.E. Holtze. Ont. Min. Env. Tech. Rept. 39 pp. Geology and Geochemistry of the Muskoka-Haliburton Study Area. Jeffries, D.S. and W.R. Snyder. Ont. Min. Env. Data Report DR 83/2. Hydrological data for lakes and watersheds in the Muskoka-Haliburton study area (1976-1980). 1983. W.A. Scheider, CM. Cox and L.D. Scott. Ont. Min. Envir. Data Report DR 83/6/. Linear Programming Screening Model for Development and Evaluation of Acid Rain Abatement Strategies. Edward A. McBean and Associates, Ltd. September, 1983. Ontario Ministry of the Environment, Policy and Planning Branch. The Macrophyte Flora of 46 Acidified and Acid Sensitive Soft Water Lakes in Ontario. Wile, I. and G. Miller. Ont. Min. Env. Tech. Rep. Meteorological Analysis of Precipitation Event Sampling Data (July 1980 - December 1981). Kurtz, J. June 1983. Morphometry of the Muskoka-Haliburton study lakes. 1983. A. Nicholls, R. Reid and R. Girard. Ont. Min. Envir. Data Report DR 83/3. Oxygen profiles on the Muskoka-Haliburton study lakes (1976-1982). 1983. R.A. Reid, R. Girard and B.A. Locke. Ont. Min. Envir. Data Report DR 83/5. 68 - 1983 (continued) A Performance and Systems Audit of the Acidic Precipitation in Ontario Study Monitoring Networks, Volume 1 and Volume 2 (Appendices). Submitted by Concord Scientific Corporation. ARB-69-83-ARSP . 1983. Phytoplankton of lakes in the Muskoka-Haliburton area. 1983. L. Nakamoto, L. Heintsch and K. Nicholls. Ont. Min. Envir. Data Report DR 83/8. Precipitation Concentration and Wet Deposition Fields of Pollutants in Ontario, September 1980 to December 1981. Chan, W.H., Tang, A.J.S. and M.A. Lusis. June 1983. A Preliminary Study for the Compilation of a VOC Emission Inventory for the Province of Ontario by Concord Scientific Corporation for MOE. Final Report CSC 110.260. June 1983. Procedures Manual - Terrestrial Effects. Griffin H.D. (Ed.). APIOS Report No. 007/83. The Province of Ontario. Presentation to the Michigan Air Pollution Control Commission in Opposition to the Consumers Power Company Request to Delay Bringing its J.H. Campbell and B.C. Cobb Power Plants into Compliance with the Michigan "One Percent or Equivalent Sulphur in Fuel" Rule. Grand Haven, Michigan. November 28, 1983. Sediment chemistry of lakes in the Muskoka-Haliburton study area. 1983. P.J. Smith. Ont. Min. Envir. Data Report DR 83/7. Studies of Lakes and Streams: Pukaskwa National Park. Sutton, J., Maki , L., Deacon, K.J. and G.W. Ozburn. API 003/83. Studies of lakes and watersheds in Muskoka-Haliburton, Ontario: methodology (1976-1982). 1983. W.A. Scheider, R.A. Reid, B.A. Locke and L.D. Scott. Ont. Min. Envir. Data Report DR 83/1. Temperature profiles on the Muskoka-Haliburton study lakes (1976-1982). 1983. R.A. Reid, B.A. Locke and R. Girard. Ont. Min. Envir. Data Report DR 83/4. Total Phosphorus and Major Ion Mass Balances for Lakes in the Muskoka- Haliburton Study Area (1976-1980). Dillon, P.J. and W.A. Scheider. Ont. Min. Env. Data Report DR 83/11. Water Quality-Crustacean Plankton Relationships in Northeastern Ontario Lakes. Keller, W. and J.R. Pitblado. API 002/83. 1982 Acid Sensitivity Survey of Lakes in Ontario. APIOS 003/82. Summer 1982. The Case Against the Rain: A Report on Acidic Precipitation and Ontario Programs for Remedial Action. Reprint with Supplementary Insert - Summer 1982. - 69 - 1982 (continued) Daily Precipitation Chemistry Listings and Statistical Summaries July 15, 1980 - December 31, 1981. APIOS 001/82. The Economics of Acid Precipitation: Ontario's Socio-economic Research Program. API 007/82. December 1982. The Effects of Acidic Precipitation on Recreation and Tourism in Ontario (2 volumes). Currie, Cooper and Lybrand Ltd. June, 1982. Ontario Ministry of the Environment. Experimental Neutralization of a Small, Seasonally Acidic Stream Using Crushed Limestone. Keller, W. and J.M. Gunn. API 004/82. Summer 1982. An Intercomparison Study of Three Precipitation Sampling Networks in Ontario - APIOS, CANSAP and GLPN. Vet, R.J., Chan, W.H. and M.A. Lusis. Report Number ARB-002-81-ARSP. Lagrangian Model of the Long Range Transport of Sulphur Oxides. API 008/82. Fall 1982. A Methodology for Estimating the Impacts of Acid Deposition in Ontario and Their Economic Value. Victor and Burrell Research and Consulting. June, 1982. Ontario Ministry of the Environment. Monitoring of Lake Superior Tributaries, 1980-1981. Keller, W. and P. Gale. API 009/82. Fall 1982. The Ontario/Canada Task Force for the Development and Evaluation of Air Pollution Abatement Options for Inco Limited and Falconbridge Nickel Mines, Limited in the Regional Municipality of Sudbury, Ontario. Fall, 1982. Ontario Ministry of the Environment. An Overview: The Cumulative Wet/Dry Deposition Network. December 1982. An Overview: The Event Wet/Dry Deposition Network. API 002/82. Summer 1982. The Province of Ontario. Presentation to the Michigan Air Pollution Control Commission in Opposition to the Detroit Edison Request to Delay Bringing its Monroe Power Plant into Compliance with the State of Michigan "^% or Equivalent Sulphur in Fuel" Rule. Monroe, Michigan. June 30, 1982. Report of the Ontario/Canada Task Force for the Development and Evaluation of Air Pollution Abatement Options for Inco Limited and Falconbridge Nickel Mines, Limited in the Regional Municipality of Sudbury, Ontario. December 21 , 1982. Standard Methods for National Wet-only Precipitation Sampling and Chemistry Analysis. McQuaker, N.R. , Kluckner, P.D., Torneby, J.E., Sorba, S.E., Chan, W.H. and M.E. Still., A Joint Report with the Federal and Other Provincial Governments. 1982. - 70 1982 (continued) A Synoptic Survey of the Acidity of Ground Waters in the Muskoka-Haliburton Area of Ontario, 1980. API 006/82. Fall 1982. A Synoptic Survey of the Acidity of Ground Waters in the Sudbury Area of Ontario, 1981. API 005/82. Fall 1982. Value, Awareness and Attitudes Associated with Acid Precipitation Effects in Ontario - The Amenity Value Survey. ARA Consultants Ltd. 1982. Ontario Ministry of the Environment. 1981 Acid Sensitivity Survey of Lakes in Ontario. API 002/81. March 1981. An Annotated Bibliography: Terrestrial Effects of Acidic Precipitation. APIOS 003/81. July 1981. Background Paper on Proposed Studies of Acid Precipitation. Ontario Ministry of the Environment. 1981. Ontario Ministry of the Environment, Program Planning and Evaluation Branch. Chemical, Microbiological and Physical Interactions of Acidic Precipitation Within a Lake and its Drainage Basin. Flett, R.J. API 004/81. July 1981 . A Critical Review of the Survey Method and Its Application. Schiff, M. 1981. Ontario Ministry of the Environment. An Intercomparison Study of Three Precipitation Sampling Networks in Ontario - APIOS, CANSAP and GLPN. Vet, R.J., Chan, W.H. and M.A. Lusis. Report No. ARB-002-81-ARSP. September 1981. Lakewide Odours in Ontario and New Hampshire Caused by Chrysochromulina breviturrita Nich. (Pymnesiophyceae) . API 001/81. 1981. Ontario Ministry of the Environment. Studies of Lakes and Watersheds Near Sudbury, Ontario: Final Limnology Report of the Sudbury Environmental Study: Volume I. Ontario Ministry of the Environment. Studies of Lakes and Watersheds Near Sudbury, Ontario: Final Limnology Report of the Sudbury Environmental Study: Volume II. Appendices. Planktonic Crustacea in Lakes in the Greater Sudbury Area. Keller, W. 1981. Ontario Ministry of the Environment Technical Report. 33 pages plus appendices. The Province of Ontario. Presentation to the Air Pollution Control Board of the State of Indiana in Opposition to the Indiana-Kentucky Electric Generating Station Petition to Operate With an Increase in its Sulphur Dioxide Emissions to 7.52 pounds of SO2 per Million BTU's of Heat Input. Indianapolis, Indiana. October 7, 1981. - 71 - 1981 (continued) The Province of Ontario. A Submission to the United States Environmental Protection Agency Hearing on Interstate Pollution Abatement. Washington, D.C. June 19, 1981. The Province of Ontario. A Submission to the United States Environmental Protection Agency on Interstate Pollution Abatement. December 1981. Docket No. A-81-09. The Province of Ontario. A Submission to the United States Environmental Protection Agency Opposing Relaxation of SO2 Emission Limits in state Implementation Plans and Urging Enforcement. March 12, 1981. Expanded March 27, 1981. The Seasonal Dependence of Atmospheric Deposition and Chemical Transformation Rates for Sulphur and Nitrogen Compounds. Lusis, M.A. and L. Shenfeld. Report No. ARB-018-ARSP . 1981. Simple Nitrogen Oxides Chemistry for Incorporation into Long Range Mathematical Models. Prepared by Concord Scientific Corporation. Report No. ARB-008-81-ARSP. February 1981. 1980 Acid Rain: A Progress Report. N.D. Yan. 1980. pp. 95-114 in C.L. Gulston (ed.) Perspectives on Natural Resources. Symposium III: Water. 6-8 Nov., 1979. Sir Sandford Fleming College, Lindsay, Ontario. Acidic Precipitation in South-Central Ontario: Analysis of Source Regions Using Air Parcel Trajectories. Kurtz, J. and W. Scheider. MOE Report, May 1980. Bulk Deposition in the Sudbury and Muskoka-Haliburton Areas of Ontario During the Shutdown of Inco Ltd. in Sudbury. Scheider, W.A., Jeffries, D.S. and P.J. Dillon. May 1980. The Case Against the Rain: A Report on Acidic Precipitation and Ontario Programs for Remedial Action. October 1980. Precipitation Sampler Comparative Study. Report No. ARB-007-81-AR5P. May 1980. 1979 Ontario Ministry of the Environment. Determination of the Susceptibility to Acidification of Poorly Buffered Surface Waters. Ont. Min. Env . Tech. Rep., 21 p. Survival of Rainbow Trout, Salmo gairdneri in Submerged Enclosures in Lakes Treated with Neutralizing Agents Near Sudbury, Ontario. Yan, N.D. , Girard, R.E. and C.L. Lafrance. Ont. Min. Env. Tech. Rep. LTS 79-2, 29 p. 72 1978 Acid Precipitation: A Review. Yan, N.D. Tech. Rep. EE-9. 35 p. Conroy, N., Hawley, K. and W. Keller. 1978. Extensive Monitoring of Lakes in the Greater Sudbury Area, 1974-76. Ontario Ministry of the Environment Technical Report. Keller, W. 1978. Limnological Observations on the Aurora Trout Lakes. Ontario Ministry of the Environment Technical Report. 49 pages. - 73 - APIOS RELATED PUBLICATIONS/PAPERS Adams, C, Egyed, M. and T. Hutchinson. 1988. Relationship between forest decline and root health in Ontario sugar maple. Proceedings Technology Transfer Conference 1988, Royal York Hotel, Toronto, Ontario. November, 1988. Environment Ontario. Session A: 15-36. Ashenden, J.E. 1989. Preliminary investigation of the influence of lake acidification on the reproductive success and feeding behaviour of the common loon in Ontario. Report to OMNR. 27 pages. Bardswick, W.S., Chan, W.H. and D.B. Orr. 1986. A Quality Assurance Program and Quality Assessment of the Acidic Precipitation in Ontario Study (APIOS) Deposition Monitoring Networks. Water, Air and Soil Pollution 30:981-990. Barrie, L.A., Lindberg, S.E., Chan, W.H., Ross, H.B., Arimoto, R. and T.M. Church. 1987. On the Concentration of Trace Metals in Precipitation Atmospheric Environment. 21:1133-1135. Beggs, G.L. and J.M. Gunn. 1986. Response of Lake Trout ( Salvelinus namaycush) and brook trout (S. fontinalis) to Surface Water Acidification in Ontario. Water Air Soil Poll. 30:711-717. Beggs, G.L., MacLean, J. A., Gunn, 3.M., Jones, M.L. and K. Minns. 1985. The Case for Effects of Acid Deposition on Ontario Fisheries. U.S. Fish Wildlife Serv. Biol. Rept . 80(40.21), 49-61. Bendell-Young, L.I., H.H. Harvey, P. 3. Dillon and P. 3. Scholer. 1989. Contrasting behaviour of manganese in the surficial sediments of 13 south-central Ontario lakes. Sci. Tot. Envir. (in press). Bisessar, S., Palmer, K.T., Kuja, A.L. and S.N. Linzon. (1984). Influence of Simulated Acidic Rain on Bacterial Speck of Tomato. Journal of Environmental Quality, Vol. 13, pp. 18-22. Bloxam, R.M., Misra, P.K. and B.E. Ley. 1986. Variable Washout Ratios in Lagrangian Models, Second APCA Specialty Conference on Meteorology of Acidic Deposition, 1986, p. 72. Booth, G.M., Hamilton, 3.G. and L.A. Molot. 1986. Liming in Ontario: Short-term Biological and Chemical Changes. Wat. Air Soil Poll. 31:709-720. Bowlby, J., Gunn, J. and V. Liimatainen. 1988. Metals in Stocked Lake Trout (Salvelinus namaycush) in Lakes Near Sudbury, Canada. Water, Air, Soil Pollut. 39:217-230. Brown, L.M., Smith, R.J., Shivers, R.R. and A.W. Day. 1986. A Re-examination of the Surface Scales of Chrysochromulina breviturrita Nicholls (Prymnesiophyceae) . Phycologia Vol. 25(4). - 74 Brydges, T.G. and G. Robinson. 1980. Two examples of urban stormwater impoundment for aesthetics and for protection of receiving waters, pp. 119-123 Jj2 Restoration of Lakes and Inland Waters, Proc. Symp. 8-12 Sept. 1980. Portland, Maine, USA, EPA 440/5-81-010. Castel, A., and C. Griffith 1986. Cost Effective Management of Wet Sulfate Deposition. Water, Air and Soil Pollution. Vol. 31:1035-1045. Chan, W.H. 1984. The Detection of Trends in Wet Deposition Data: Report of a Workshop, Section 3-1. Environmental Monograph No. 4, University of Toronto, R.E. Munn (Rapporteur). Chan, W.H. 1982. Quality Assurance - Monitoring of Wet Deposition. Presented at the Symposium on Monitoring and Assessment of Airborne Pollutants with Special Emphasis on Long-Range Transport and Deposition of Acidic Materials, National Research Council of Canada, Ottawa, Ontario, August 30 - September 1, 1982. Chan, W.H. 1982. Sudbury Environmental Study - Atmospheric Research Program. Report ARB-27-82-AR5P . Chan, W.H. and D.H.S. Chung. 1986. Regional Scale Precipitation Scavenging of SO2, SO4, NO3 and HNO3. Atmospheric Environment 20:1397-1402. Chan, W.H. and M.A. Lusis. 1986. Smelting Operations and Trace Metals in Air and Precipitation in the Sudbury Basin in "Toxic Metals in the Air". Nriagu, J.O. and C.I. Davison, (Eds.), John Wiley and Sons. Chan, W.H. and M.A. Lusis. 1985. Post-Superstack Sudbury Smelter Emissions and Their Pate in the Atmosphere: An Overview of the Sudbury Environmental Study. Water, Air and Soil Pollution 26:43-58. Chan, W.H., Lusis, M.A., Stevens, R.D.S. and R.J. Vet. 1984. A Precipitation Sampler Intercomparison. Water, Air and Soil Pollution 23:1-13. Chan, W.H., Orr, D.B. and D.H.S. Chung. 1986. An Evaluation of Artifact SO4 Eormation on Nylon Eilters under Field Conditions. Atmospheric Environment 20:2397-2401. Chan, W.H., Ro, C.U., Vet, R.J., Tang, A. J. 5. and M.A. Lusis. 1983. Precipitation Scavenging and Dry Deposition of Pollutants from the Inco Nickel Smelter in Sudbury. Proceedings of the 4th International Conference on Precipitation Scavenging, Dry Deposition and Resuspension, G. Slinn, (Ed.), Elsevier Science Publishing Co. Inc., 1983. Chan, W.H., Tang, A.J.S., Chung, D.H.S. and M.A. Lusis. 1982. Concentration and Deposition of Trace Metals in Ontario - 1982. Water, Air and Soil Pollution 29:373-389. Chan, W.H., Tang, A.J.S., Chung, D.H.S., and N.W. Reid. 1987. An analysis of Precipitation Chemistry Measurements in Ontario. Env . Sci. Technol. 21:1219-1224. - 75 - Chan, W.H., Tang, A.J. and M.A. Lusis. 1983. Precipitation Concentration and Wet Deposition Fields of Pollutants in Ontario, 1981. Report ARB-61-83-ARSP. Chan, W.H., Tomassini, F. and B. Loescher. 1983. An Evaluation of Sorption Properties of Precipitation Constituents on Polyethylene Surfaces. Atmospheric Environment 17:1779-1785. Chan, W.H., Vet, R.J., Lusis, M.A., Hunt, J.E. and R.D.S. Stevens. 1980. Airborne Estimation of Particulate Emissions from Stacks: A Feasibility; Study. Atmospheric Environment 14:1201-1203. Chan, W.H., Vet, R.J., Lusis, M.A., Hunt, J.E. and R.D.S. Stevens. 1980. Airborne Sulphur Dioxide to Sulphate Oxidation Studies of the Inco 381 m Chimney Plume. Atmospheric Environment 14:1159-1170. Chan, W.H., Vet, R.J., Lusis, M.A. and G.B. Skelton. 1983. Airborne Particulate Size Distribution Measurements in Nickel Smelter Plumes. Atmospheric Environment 17:1173-1181. Chan, W.H., Vet, R.J., Lusis, M.A. and G.B. Skelton. 1982. Size Distribution and Emission Rate Measurements of Particulates in the Inco 381 M Chimney and Iron Ore Recovery Plant Stack Plumes, 1979-80. Report ARB-TDA-62-80. Chan, W.H., Vet, R.J., Ro, CD. and M.A. Lusis. 1982. Impact of the Inco Nickel Smelter Emissions on Precipitation Quality in the Sudbury Area. Atmospheric Environment 16:801-814. Chan, W.H., Vet, R.J., Ro, C.U., Tang, A.J.S. and M.A. Lusis. 1984. Impact of Inco Smelter Emissions on Wet and Dry Deposition in the Sudbury Area. Atmospheric Environment 18:1001-1008. Chan, W.H., Vet, R.J., Ro, C.U., Tang, A.J.S. and M.A. Lusis. 1984. Impact of Smelting Activities on Long-Term Precipitation Quality and Wet Deposition Fields in the Sudbury Basin. Atmospheric Environment 18:1175-1188. Chan, W.H., Vet, R.J., Ro, CO., Tang, A.J.S. and M.A. Lusis. 1982. An Analysis of the Impact of Smelter Emissions on Atmospheric Dry Deposition in the Sudbury Area: Sudbury Environmental Study Airborne Particulate Matter Network Results. Report ARB-012-81-ARSP. Chan, W.H., Vet, R.J., Ro, C.U., Tang, A.J.S. and M.A. Lusis. 1982. An Analysis of the Impact of Smelter Emissions on Precipitation Quality and Wet Deposition in the Sudbury Area: Sudbury Environmental Study Event Precipitation Network Results. Report ARB-0 5-82-ARSP. Chan, W.H., Vet, R.J., Ro, C.U., Tang, A.J.S. and M.A. Lusis. 1982. Precipitation Quality and Wet Deposition in the Sudbury Basin: Sudbury Environmental Study Cumulative Precipitation Network Results. Report ARB-04-82-ARSP. 76 - Chan, W.H., Vet, R.3., Skelton, G.B. and M.A. Lusis. 1982. Size Distribution and Emission Rate Measurements of Particulates in the 93 M Falconbridge Smelter Stack Plume, 1979. Report ARB-TDA-57-80. Clark, K.L. and R.J. Hall. 1985. Effects of Elevated Hydrogen Ion and Aluminum on Survival of Amphibian Embryos and Larvae. Can. J. Zool. 63:116-123. Clark, K.L. and B.D. LaZerte. 1987. Intraspecif ic Variation in Hydrogen Ion and Aluminum Toxicity in Bufo americanus and Ambystoma maculatum. Can. J. Fish, and Aquat. Sci. 44:1622-1628. Clark, K.L. and B.D. LaZerte. 1985. A Laboratory Study of the Effects of Aluminum and pH on Amphibian Eggs and Tadpoles. Can. J. Fish. Aquat. Sci. 42:1544-1551. Conroy, N., Hawley, K., Keller, W. and C. Lafrance. 1976. Influences of the Atmosphere on Lakes in the Sudbury Area. Proc. First Spec. Symp. on Atmospheric Assoc. Great Lakes Res. 2:146-165. Conroy, N., Jeffries, D.S. and J.R. Kramer. 1974. Acid Shield Lakes in the Sudbury, Ontario Region. Proceedings of 9th Canadian Symposium on Water Pollution Research in Canada No. 9, pp. 45-61. Conroy, N., and W. Keller. 1976. Geological Factors Affecting Biological Activity in Precambrian Shield Lakes. Canadian Mineral 14:62-72. Craig, G.R. and W.F. Baksi. 1977. The Effects of Depressed pH on Flagfish Reproduction, Growth and Survival. Wat. Res. 11:621-626. Cunningham, G.L. and B.J. Shuter. 1986. Interaction of Low pH and Starvation on Body Weight and Composition of Young-of-the-year Smallmouth Bass (Micropterus dolomieui). Can. J. Fish. Aquat. Sci. 43:869-876. de Grosbois, E., Dillon, P.J., Seip, H.M., and H. Seip. 1986. Modelling Hydrology and Sulphate Concentration in Small Catchments in Central Ontario. Wat. Air Soil Pollut. 31:45-58. de Grosbois, E., R.P. Hooper and N. Christophersen. A multisignal automatic calibration methodology for hydrochemical models: a case study of the Birkenes model. Water Resourc. Res. 24:1299-1307. Devito, K.J., P.J. Dillon and B.D. LaZerta. 1988. Phosphorus and Nitrogen Retention in Five PreCambrian Shield Wetlands. Biogeochem. (in press). Dillon, P.J. 1984. The Use of Mass Balances and Mass Balance Models for Quantification of the Effects of Anthropogenic Activities on Lakes Near Sudbury, Ontario, pp. 283-347, _in Environmental Impacts of Smelters, J. Nriagu, (Ed.), Advances in Environmental Science Series, John Wiley and Sons, Inc. Dillon, P.J. 1983. Chemical Alterations of Surface Waters by Acidic Deposition in Canada. Wat. Qual. Bull. 8:127-132. - 11 - Dillon, P.J., Evans, H.E. and P.J. Scholer. 1988. The Effects of Acidification on Metal Budgets of Lakes and Catchments. Biogeochemistry. 5:201-220. Dillon, P.J. and R.D. Evans. 1982. Whole-lake Lead Burdens in Sediments of Lakes in Southern Ontario, Canada. Hydrobiol. 91:121-130. Dillon, P.3., Jeffries, D.S. and W.A. Scheider. 1982. The Use of Calibrated Lakes and Watersheds for Estimating Atmospheric Deposition Near a Large Point Source. Wat. Air Soil Pollut. 18:241-258. Dillon, P.J., Jeffries, D.S., Scheider, W.A. and N.D. Yan. 1980. Some Aspects of Acidification in Southern Ontario, p. 212-213, in "Proc. Int. Conf. Ecol. Impact Acid Precip.", Drablos, D. and A. Tollan~TEds. ) , Norway. Dillon, P.J., Jeffries, D.S., Snyder, W., Reid, R. , Yan, N.D., Evans, D. , Moss, J. and W.A. Scheider. 1978. Acidic Precipitation in South-Central Ontario: Recent Observations. J. Fish. Res. Board. Can. 35:809-815. Dillon, P.J., Lusis, M.A., Reid, R.A. and D. Yap. 1988. Ten-year Trends in Sulphate, Nitrate and Hydrogen Deposition in Central Ontario. Atmos. Environ. 22:901-905. Dillon, P.J. and L.A. Molot. 1989. The role of ammonium and nitrate retention in the acidification of lakes and forested catchments. Biogeochem. (in press). Dillon, P.J., K.H. Nicholls and G. Robinson. 1978. Phosphorus removal at Gravenhurst Bay, Ontario: an 8-year study on water quality changes. Verb. Internat. Verein. Limnol. 20:263-271. Dillon, P.J., Nicholls, K.H., Locke, B.A., de Grosbois, E. and N.D. Yan. 1988. Phosphorus-phytoplankton Relationships in Nutrient-poor Soft-water Lakes in Canada. Verb. Verein Internat. Limnol. 23:258-264. Dillon, P.J. and R.A. Reid. 1981. The input of biologically available phosphorus by precipitation to Precambrian lakes, pp. 183-198 in_ Atmospheric Input of Pollutants to Natural Waters, S. Eisenreich (ed.), Ann Arbor Science. Dillon, P.J., Reid, R.A. and E. de Grosbois. 1987. The Rate of Acidification of Aquatic Ecosystems in Ontario, Canada. Nature 329:45-48. Dillon, P.J., Reid, R.A. and R. Girard. 1986. Changes in the Chemistry of Lakes Following Reductions of SO2 Emissions. Wat. Air Soil Pollut. 31:59-66. Dillon, P.J. and W.A. Scheider. 1984. Modelling the Reacidification Rates of Neutralized Lakes Near Sudbury, Ontario, pp. 121-154, _in Modelling of Total Acid Precipitation Impacts, Schnoor, J.L. (Ed.), Acid Precipitation Series, Volume 9, Ann Arbor Science. - li Dillon, P. 3. Scholer, P.J. and H.E. Evans. 1986. Lead-210 Fluxes in Acidified Lakes. 3. Environ. Geol. Wat. Sci. Sediments and Water Interactions pg. 491-499 ed P. Sly. Dillon, P. 3. and P. 3. Smith. 1984. Trace Metal and Nutrient Accumulation in the Sediments of Lakes Near Sudbury, Ontario, pp. 375-426, j£i^ Environmental Impact of Smelters, Nriagu, 3., (Ed.), Advances in Environmental Science Series, 3ohn Wiley and Sons, Inc. Dillon, P. 3., Yan, N.D. and H.H. Harvey. 1984. Acidic Precipitation: Effects on Aquatic Ecosystems. CRC Critical Reviews in Environmental Control 13:167-194. Dillon, P. 3., Yan, N.D., Scheider, W.A. and N. Conroy. 1979. Acidic Lakes in Ontario, Canada: Characterization, Extent and Responses to Base and Nutrient Additions. Arch. Hydrob. Beih, Ergebn. Limnol. 13:317-336. Dodge, D.P., Booth, G.M., Richman, L.A., Keller, W., and F.D. Tomassini, 1988. An overview of lake neutralization experiments in Ontario, 1981 - 1987. Water Air, Soil Poll. 41 ( 1-4) :75-84. Ellenton, G., Ley, B.E. and P.K. Misra. 1985. A Trajectory Puff Model of Sulphur Transport for Eastern North America. Atmospheric Environment 19:727-737. Ellenton, G., Ley, B.E. and P.K. Misra. 1983. Treating Exponential Mass Decay When Wet Scavenging Varies Discreetly Within an Expanding Gaussian Dispersed Puff. The Meteorology of Acid Deposition, Samson, P. 3., (Ed.), Proceedings of an APCA Specialty Conference, pp. 528-536. Ellenton, G. Misra, P.K., and Ley, B. (1988). The Relative Roles of Emission Changes and Meteorological Variability in Variation of Wet Sulphur Deposition. A Trajectory Model Study. Atmospheric Environment, 22, 547-556. Enyedi, A. 3. and A.L. Kuja. 1986. Assessment of Relative Sensitivities During Early Growth Stages of Selected Crop Species Subjected to Simulated Acidic Rain. Water, Air and Soil Pollution 31:325-335. Evans, R.D. and P. 3. Dillon. 1982. Historical Changes in Anthropogenic Lead Fallout in Southern Ontario, Canada. Hydrobiol. 91:131-137 Evans, H.E., Dillon, P. 3., Scholer, P. 3. and R.D. Evans. 1986. The use of Pb/210pt-) ratios in lake sediments for estimating atmospheric fallout of stable lead in south-central Ontario, Canada. Sci. Tot. Envir. 54:77-93. Evans, H.E., Lasenby, D.C. and P. 3. Dillon. 1986. The Effect of Core Compression on the Measurement of Zinc Concentrations and Anthropogenic Burdens in Lake Sediments. Hydrobiol. 132:185-192. - 79 - Evans, H.E., Smith, P.J. and P.O. Dillon. 1983. Anthropogenic Zinc and Cadium Burdens in Sediments of Selected Southern Ontario Lakes. Can. J. Fish. Aquat. Sci. 40:570-579. France, R.L. and B.D. LaZerte. 1987. Empirical Hypothesis to Explain the Restricted Distribution of Hyalella azteca (Amphipoda) in anthropogenically acidified lakes. Can. J. Fish. Aquat. Sci. 44:1112-1121. Freda, J., M.E. MacDougall, and V. Glooschenko. Amphibian breeding ponds in the Sudbury region: chemical characterization and toxicity of 3 species of amphibians. Can. 3. Fish. Aquatic Sci. Submitted. Freda, J., V. Cavdek, and D.G. McDonald. The role of organic complexation in the toxicity of metals to amphibians. Can. 3. Fish. Aquat. Sci. Submitted. Freda, 0. and D.G. McDonald 1989. The effects of aluminum on amphibians; life cycle comparisons and aluminum uptake. Can. 3. Fish. Aquat. Sci. In press. Fung, C, Misra, P.K., Bloxam, R. and Wong, 5. (1989) Non-linear Response of Wet Deposition to Emission Reduction. A Model Study. Sixth Joint Conference on Application of Air Pollution meteorology, Anaheim Calif., Jan. 30 - Feb. 3. Galloway, J.N. and P.J. Dillon. 1983. Effects of Acidic Deposition: The Importance of Nitrogen. Ecological Effects of Acid Deposition. Nat. Swedish Envir. Protection Bd. - Report PM 1636:145-160. Giberson, D.J. and R.J. Hall. 1988. Spatial and Temporal Distribution of the Fauna in the Sediments of a Canadian Shield Lake Outflow Stream. J. Can. Fish. Aq. Sci. 45:1994-2002. Glass, G.E. and T.G. Brydges. 1982. Problem Complexity in Predicting Impacts from Altered Precipitation Chemistry. _In Acid Rain/Fisheries, Johnson, R.E., (Ed.), American Fisheries Society, Bethesda, Md., pp. 265-286. Glass, G.E., Leonard, E.N., Chan, W.H. and D.B. Orr. 1986. Airborne Mercury in Precipitation in the Lake Superior Region. Journal of the International Association for Great Lakes Research 12:37-51. Glooschenko, V., Downes, C, Frank, R., Braun, H.E., Addison, E.M. and J. Hickie. 1988. Cadmium Levels in Ontario Moose and Deer in Relation to Soil Sensitivity to Acid Precipitation. Science of the Total Environment 71:173-186. Glooschenko, V., Frank, R., Downes, CM., Braun, H.E., Addison, E.M. and J. Hickie. 1987. Cadmium levels in Ontario moose and the implications for human resource users. Proceedings of the 6th International Conference for Heavy Metals in the Environment. New Orleans, LA, U.S.A., September 1988. 80 Glooschenko, V., Weller, W., Smith, P.G.R., Alvo, R. and Archbold, 3. and A. Bleiwks. Amphibian distribution with respect to pond water chemistry near Sudbury, Ontario. Can. 3. Zoology. Submitted. Gunn, 3.M. 1989. Survival of Lake Charr (Salvelinus Namaycush) Embryos Under Pulse Exposure to Acidic Runoff Water ln_ Aquatic Toxicity and Water Quality Management, 3. Nriagu (ed.), 3ohn Wiley and Sons Inc. Gunn, 3.M. 1986. Behaviour and Ecology of Salmonid Fishes Exposed to Episodic pH Depressions. Env. Biol. Fish. 17:241-252. Gunn, 3.S., Deacon, L., Stewart, T., Hicks, F., MacKay, L., Munroe, B. and G. Beggs. 1988. Trend-through-time Monitoring of Fish Communities n Acid Sensitive Lakes in Ontario. Lake Reservoir Management 4( 1 ) :123-1 34. Gunn, 3.M. and W. Keller. 1986. Effects of acidic meltwater on chemical conditions at nearshore spawning sites. Wat. Air Soil Pollut. 30:545-552. Gunn, 3.M. and W. Keller. 1985. Effects of Ice and Snow Cover on the Chemistry of Nearshore Lake Water During Spring Melt. Annals of Glaciology 7:208-212. Gunn, 3.M. and W. Keller. 1984. In Situ Manipulation of Water Chemistry Using Crushed Limestone and Observed Effects on Fish. Fisheries 9:19-24. Gunn, 3.M. and W. Keller. 1984. Spawning Site Water Chemistry and Lake Trout (Salvelinus namaycush) Sac Fry Survival During Spring Snowmelt. Can. 3. Fish. Aquat. Sci. 42:319-329. Gunn, 3.M. and W. Keller. 1981. Emergence and Survival of Lake Trout (Salvelinus namaycush) and Brook Trout (_S. fontinalis) from Artificial Substrates in an Acid Lake. Ontario Fisheries Technical Report Series, 1, Toronto. Gunn, 3.M. and W. Keller. 1980. Enhancement of the Survival of Rainbow Trout (Salmo gairdneri ) Eggs and Fry in an Acid Lake through Incubation in Limestone"! Can. 3. Fish. Aquat. Sci. 37:1522-1530. Gunn, 3.M., McMurtry, M., Bowby, 3., Casselman, 3. and V. Liimatainen. 1987. Survival and Growth of Stocked Lake Trout in Relation to Body Size, Stocking Season, Lake Acidity, and Biomass of Competitors. Trans. Amer. Fish. Soc. 116:618-627. Gunn, 3.M. and D.L.G., Noakes 1986. Avoidance of low pH and Elevated Al Concentrations by Brook Charr (Salvelinus fontinalis) alevins in laboratory tests. Water Air, Soil Poll. 30:497-503. Gunn, 3.M. and D.L.G. Noakes. 1987. Latent Effects of Pulse Exposure to Aluminum and Low pH on Size, Ionic Composition and Feeding Efficiencies of Lake Trout (Salvelinus namaycush) alevins. Can. 3. Fish. Aquat. Sci. 45:1418-1424. Gunn, 3.M., Noakes, D.L.G. and G.L. Westlake. 1987. Behavioural Responses of Lake Charr (Salvelinus namaycush) Embryos to Simulated Acidic Runoff Conditions. Can 3. Zool. 65:2786-2792. - 81 Gunn, J.M., Hamilton, 3.G., Booth, CM., Wren, CD., Beggs, CL., Rietveld, H.3. and J.R. Munro, 1989. Survival, Growth and Reproduction of Lake Trout (Salvelinus namaycush) , and Yellow Perch (Perce flauescens) after neutralization of an acidic lake near Sudbury, Ontario. Can. J. Fish. Aquatic Sci. (in press). Gunn, J.M., McMurtry, M.J., Casselman, J.M., Keller, W. and M.J. Powell. 1988. Changes in the fish community of a limed lake near Sudbury, Ontario: effects of chemical neutralization or reduced atmospheric deposition of acids? Wat. Air, Soil Pollut. 41 ( 1-4) : 1 1 3-1 36. Hall, R.J., Findeis, 3. and R.C Bailey. 1988. Factors Affecting Survival and Cation Concentration in the Blackflies Prosimuluim fuscum/mixtum and the mayfly Leptophlebia cuspida During Spring Snowmelt. J. Can. Fish. Aq. Sci. 45:2123-2132. Hall, R.3. and F.P. Ide. 1987. Evidence of Acidification Effects on Stream Insect Communities in Central Ontario Between 1937 and 1985. Can. 3. Fish. Aquat. Sci. 44:1652-1657. Harvey, H.H., Pierce, R.C, Dillon, P. 3., Kramer, 3. P. and D.M. Whelpdale. 1981. Acidification in the Canadian Aquatic Environment. Publ. NRCC No. 18475 of the Environment Secretariat, National Research Council, Canada. Heidorn, K.C and D. Yap. 1986. A Synoptic Climatology for Surface Ozone Concentrations in Southern Ontario, 1976 - 1981. Atmospheric Environment 20:695-703. Hendry, CR., Yan, N.D. and K.3. Baumgartner. 1980. Responses of Freshwater Plants and Invertebrates to Acidification, pp. 457-466. ln_ "Restoration of Lakes and Inland Waters". Proc. Symp. 8-12 September 1980. Portland, Maine, U.S.A. EPA 440 15-81-010. Holtze, K.E. and N.3. Hutchinson. 1989. Lethality of low pH and Al to early life-stages of six fish species inhabiting PreCambrian Shield waters in Ontario. Can. 3. Fish. Aquat. Sci. 46: 1188-1202. Hulsman, P., Powles, P. and 3. Gunn. 1983. Mortality of Walleye Eggs and Rainbow Trout Yolk Sac Larvae in Low pH Waters of the LaCloche Mountain Area. Trans. Amer. Fish. Soc. 112:680-688. Hutchinson, N.3., Holtze, K.E., Munro, 3.R. and T.W. Pawson. 1988. Modifying Effects of Life Stage, Ionic Strength and Post-exposure Mortality on Lethality of H"'' and Al to Lake Trout and Brook Trout. Aquat. Tox. 15:1-26. Hutchinson, N.3., Holtze, K.E., Munro, 3.R. and T.W. Pawson. 1987. Lethal Responses of Salmonid Early Life Stages to H"*" and Al in Dilute Waters. In H. Witters and 0. Vanderborght (eds.), Ecophysiology of Acid Stress in Aquatic Organisms. Annis Soc. r. zool. Belg. - Vol. 117 (1987) supplement 1 . 82 Imhof, J.G., N. Kaushik, 3. Bowlby, A. Gorden and R.3. Hall. 1989. Natural River Ecosystems: The ultimate integrators. Proceedings of the Management of Ontario Streams, Toronto, Ontario. Jacobson, J., Irving, P., Kuja, A., Lee, 3., Shriner, D., Troiano, 3., Perrigan, S. and V. Cullinan. 1988. A Collaborative Effort to Model Plant Response to Acidic Rain. 3APCA 38:777-783. 3effries, D.S. 1984. Atmospheric Deposition of Pollutants in the Sudbury Area. pp. 117-154, Jjl Environmental Impacts of Smelters, Nriagu, J., (Ed.), Advances in Environmental Impacts of Science Series, 3ohn Wiley and Sons, Inc. 3effries, D.S., Cox, CM. and P. 3. Dillon. 1979. Depression of pH in Lakes and Streams in Central Ontario During Snowmelt. 3. Fish. Res. Board. 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